appendix k - part c · ), wild yellow jasmine (pittosporum revolutum), narrow-leaved geebung...

Appendix K - Part C SKM (2013) Biodiversity Assessment

Upgrade of the Princes Highway Dignams Creek Appendix K Review of Environmental Factors

Upgrade of the Princes Highway, Dignams Creek –Biodiversity Assessment

Appendix A Vegetation community descriptions Map Unit 1: Silvertop Ash - Stringybark Dry Open Forest

General Description: This community occurs on exposed ridges and slopes of the study area. This community is dominated by the tree species Silvertop Ash (Eucalyptus sieberi) and Blue-leaved Stringybark (Eucalyptus agglomerata) with several other canopy species generally occurring in lower abundance. This includes White Stringybark (Eucalyptus globoidea), Rough-barked Apple (Angophora floribunda) and Mugga Ironbark (Eucalyptus tricarpa); however these species are co-dominant in some areas of this map unit. In places there is a sub-canopy of Black She-oak (Allocasuarina littoralis), in particular where there has been pas t disturbance from logging activities.

The understorey is dominated by various shrubs and grasses. Dominant shrub species include Gorse Bitter-pea (Daviesia ulicifolia), Spiny Bossiaea (Bossiaea obcordata), Narrow-leaved Geebung (Persoonia linearis) and Shrubby Platysace (Platysace lanceolata). Dominant groundcover species include grasses Kangaroo Grass (Themeda australis), Threeawn Speargrass (Aristida vagans), Blady Grass (Imperata cylindrica) and Wiry Panic (Entolasia stricta), and forb species Pomax (Pomax umbellata), Many-flowered Mat-rush (Lomandra multiflora subsp. multiflora) and Blue Bottle-daisy (Lagenophora stipitata).

Dominant Canopy Species: Eucalyptus sieberi, Eucalyptus agglomerata (18-20 m)

Small Tree Species: Allocasuarina littoralis

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Dominant Shrub Species: Daviesia ulicifolia, Persoonia linearis, Platysace lanceolata, Podolobium ilicifolium, Acacia obtusifolia, Leucopogon lanceolatus, Bossiaea obcordata, Ozothamnus diosmifolius, Hibbertia aspera, Acacia terminalis, Correa reflexa

Common Groundcover Species: Aristida vagans, Themeda australis, Imperata cylindrica, Dianella caerulea, Entolasia stricta, Joycea pallida, Lepidosperma laterale, Lomandra confertifolia subsp. similis, Lomandra multiflora subsp. multiflora, Lagenophora stipitata

Equivalent Map Units: Regional: DSF e32A Deua-Brogo Foothills Dry Shrub Forest and DSF e32B Far South Coastal Foothills Dry Shrub Forest (Tozer et al. 2010) Biometric: Silvertop Ash - Blue-leaved Stringybark - Woollybutt shrubby open forest on coastal foothills central South East Corner State: South East Dry Sclerophyll Forest

Conservation Status: Common vegetation community with >95% of the original extant (42,200 ha) of this community estimated to remain and well represented in conservation reserves with 60-70% (27,700 ha) of the original pre-European extant in conservation reserves (Tozer et al. 2010).

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Map Unit 2: White Stringybark Forest

General Description: This community occurs on less exposed slopes of the study area, in the areas in between the more exposed slopes of map unit 1 and sheltered gully areas of map unit 3. This community is dominated by White Stringybark (Eucalyptus globoidea), however canopy species from both Map Unit 1 and 3 ar e present in this community and are often co-dominant particularly Rough-barked Apple (Angophora floribunda) and Yellow Stringybark (Eucalyptus muelleriana). In places there is an open to dense sub-canopy of Black She-oak (Allocasuarina littoralis), in particular where there has been past disturbance from logging activities. In areas Broad-leaved Hickory (Acacia falciformis), Sweet Pittosporum (Pittosporum undulatum) and Acacia irrorata also forms part of the subcanopy of this map unit.

This understorey supports a mix of shrubs and groundcovers many of which occur in Map Unit 1 and 3. Dominant shrub species include Coffee Bush (Breynia oblongifolia), Wild Yellow Jasmine (Pittosporum revolutum), Narrow-leaved Geebung (Persoonia linearis), Leucopogon lanceolatus var. lanceolatus, Shrubby Platysace (Platysace lanceolata) and Rough Guinea Flower (Hibbertia aspera). Dominant groundcovers include Weeping Grass (Microlaena stipoides), Bordered Panic (Entolasia marginata), Stinking Pennywort (Hydrocotyle laxiflora) and Kidney Weed (Dichondra repens).

Dominant Canopy Species: Eucalyptus globoidea, Angophora floribunda, Eucalyptus botryoides x saligna, Eucalyptus muelleriana, Eucalyptus cypellocarpa, Eucalyptus bosistoana (20-25 m)

Small Tree Species: Allocasuarina littoralis, Acacia falciformis, Acacia irrorata Pittosporum undulatum

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Dominant Shrub Species: Breynia oblongifolia, Pittosporum revolutum, Persoonia linearis, Leucopogon lanceolatus var. Lanceolatus, Platysace lanceolata, Hibbertia aspera, Cassinia trinervia, Pomaderris aspera, Notelaea venosa, Polyscias sambucifolia

i. Common Groundcover Species: Microlaena stipoides, Oplismenus aemulus, Entolasia marginata, Poa ensiformis, Hydrocotyle laxiflora, Dichondra repens, Schelhammera undulata, Gahnia melanocarpa

Common Climber Species: Marsdenia rostrata, Pandorea pandorana, Calystegia marginata, Clematis glycinoides

Equivalent Map Units: Regional: WSF e34: Southeast Coastal Gully Shrub Forest (Tozer et al. 2010) Biometric: Coast Grey Box - Mountain Grey Gum - Stringybark moist shrubby open forest in coastal gullies, southern South East Corner State: South Coast Wet Sclerophyll Forests (Keith 2006)

Conservation Status: A relatively common vegetation community with >85% of the original extant (22,800 ha) of this community estimated to remain and relatively well represented in conservation reserves with 25-35% (6,900 ha) of the original pre-European extant estimated to occur in conservation reserves (Tozer et al. 2010).

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Map Unit 3: Bangalay/Blue Gum Sheltered Forest

General Description: This map unit occurs in sheltered gullies and s lopes of the study area. This community is dominated by a mix of canopy species with Bangalay/Blue Gum (Eucalyptus botryoides x saligna) being consistently present. Other dominant species comprise Yellow Stringybark (Eucalyptus muelleriana), Rough-barked Apple (Angophora floribunda), Monkey Gum (Eucalyptus cypellocarpa), White Stringybark (Eucalyptus globoidea) and River Peppermint (Eucalyptus elata). Some areas of this community have an open s ub-canopy of small tree species including Grey Myrtle (Backhousia myrtifolia), Sweet Pittosporum (Pittosporum undulatum), Scentless Rosewood (Synoum glandulosum) and B lueberry Ash (Elaeocarpus reticulatus).

The understorey is dominated by a mix of mesic shrubs and groundcovers. Dominant species include: shrubs such as Tree Violet (Melicytus dentatus), Hazel Pomaderris (Pomaderris aspera) and Cassinia trinervia; fern species such as Soft Bracken (Calochlaena dubia), Prickly Rasp-fern (Doodia aspera), Gristle Fern (Blechnum cartilagineum) and R ough Tree-fern (Cyathea australis); grasses and forbs such as Basket Grass (Oplismenus aemulus), Margined Panic (Entolasia marginata), Purple-sheathed Tussock-grass (Poa ensiformis), Stinking Pennywort (Hydrocotyle laxiflora) and Lilac Lily (Schelhammera undulata); and nu merous vine species including Water Vine (Cissus antarctica), Common Milk Vine (Marsdenia rostrata) and Morinda (Morinda jasminoides).

Dominant Canopy Species: Eucalyptus botryoides x saligna, Eucalyptus muelleriana, Angophora floribunda, Eucalyptus cypellocarpa, Eucalyptus elata, Eucalyptus globoidea (20-25 m)

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Small Tree Species: Backhousia myrtifolia, Synoum glandulosum, Elaeocarpus reticulatus, Pittosporum undulatum, Cyathea australis

Dominant Shrub Species: Cassinia trinervia, Melicytus dentatus, Pomaderris aspera, Notelaea venosa, Ozothamnus argophyllus, Calochlaena dubia

Common Groundcover Species: Oplismenus aemulus, Entolasia marginata, Poa ensiformis, Hydrocotyle laxiflora, Schelhammera undulata, Doodia aspera, Blechnum cartilagineum, Gahnia melanocarpa, Lomandra longifolia, Oplismenus imbecillis

Common Climber Species: Cissus antarctica, Marsdenia rostrata, Morinda jasminoides

Equivalent Map Units: Regional: WSF n183: South Coast Hinterland Wet Forest (Tozer et al. 2010) Biometric: Mountain Grey Gum - Yellow Stringybark moist shrubby open forest in gullies of the coastal ranges, northern South East Corner State: South Coast Wet Sclerophyll Forests (Keith 2006)

Conservation Status: Common vegetation community with >95% of the original extant (69,400 ha) of this community estimated to remain and relatively well represented in conservation reserves with 40-50% (30,300 ha) of the original pre-European extant estimated to occur in conservation reserves (Tozer et al. 2010).

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Map Unit 4: River Peppermint - Rough-barked Apple moist shrubby forest

General Description: This map unit occurs on a steep sheltered slope above Dignams Creek at the north-eastern end of the study area. This community is dominated by River Peppermint (Eucalyptus elata) and Rough-barked Apple (Angophora floribunda). This community has a relatively dense subcanopy including Sweet Pittosporum (Pittosporum undulatum), Mock Olive (Notelaea venosa) and Brush Muttonwood (Myrsine howittiana).

The majority of this community in the study area is in a low-moderate condition, being underscrubbed and u sed for cattle grazing. There is a relatively dense shrub layer in areas including Tree Violet (Melicytus dentatus), Tall Paper Daisy (Ozothamnus diosmifolius), Wild Yellow Jasmine (Pittosporum revolutum) and Orange Thorn (Pittosporum multiflorum). The ground layer is relatively sparse due t o shading from the dense subcanopy and shrub layers, including a diversity of shade tolerant species such as fern species such as Prickly Rasp-fern (Doodia aspera) and Gristle Fern (Blechnum cartilagineum), grasses and forbs such as Basket Grass (Oplismenus aemulus), Weeping Grass (Microlaena stipoides), Lilac Lily (Schelhammera undulata) and Ivy-leaf Violet (Viola hederacea).

Dominant Canopy Species: Eucalyptus elata, Angophora floribunda, Eucalyptus botryoides x saligna (20-25 m)

Small Tree Species: Pittosporum undulatum, Notelaea venosa, Myrsine howittiana

Dominant Shrub Species: Melicytus dentatus, Pittosporum multiflorum, Ozothamnus diosmifolius, Pittosporum revolutum

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Common Groundcover Species: Oplismenus aemulus, Schelhammera undulata, Doodia aspera, Blechnum cartilagineum, Microlaena stipoides, Viola hederacea

Equivalent Map Units: Regional: DSF e19: Bega Wet Shrub Forest (Tozer et al. 2010) Biometric: River Peppermint - Rough-barked Apple moist open forest on sheltered sites, southern South East Corner State: Southern Hinterland Dry Sclerophyll Forests (Keith 2006)

Conservation Status: This community has been subjected to substantial disturbance and clearing with 35-50% of the pre-European extant estimated to remain (Tozer et al. 2010). It is represented in conservation reserves with 5-15% of the original pre-European extant estimated to occur in conservation reserves (Tozer et al. 2010).

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Map Unit 5: Riparian Forest

General Description: This community occurs as a t hin edge-effected riparian strip along Dignams Creek and i ntact examples of this community are present along Blinds Creek. This community is dominated by River Oak (Casuarina cunninghamiana) along Dignams Creek and River Peppermint (Eucalyptus elata) on Blind Creek. Other canopy species present along Dignams Creek and B lind Creek include Bangalay/Blue Gum (Eucalyptus botryoides x saligna) and Rough-barked Apple (Angophora floribunda). Smaller tree species include White Sally Wattle (Acacia floribunda), Black Wattle (Acacia mearnsii), Cassinia trinerva and Brush Kurrajong (Commersonia fraseri).

Areas of this community along Dignams Creek are highly disturbed from clearing and grazing supporting a diversity of weeds. Dominant shrub species include Tree Violet (Melicytus dentatus), Twin-flower Tea-tree (Leptospermum emarginatum), the threatened Square Raspwort (Halorgris exaltata subsp. exaltata) and Fireweed Groundsel (Senecio linearifolius). Groundcovers include a diversity of flora species including: fern species such as Fishbone Water Fern (Blechnum nudum) and Maidenhair Fern (Adiantum aethiopicum); grasses and graminoids include Basket Grass (Oplismenus aemulus) and Mat Rush (Lomandra longifolia); and f orb species such as Austrocynoglossum latifolium, Native Violet (Viola hederacea), Spotted Knotweed (Persicaria decipiens). There is a diversity exotic species present along Dignams Creek including common pasture plants such as White Clover (Trifolium repens) and Kikuyu (Pennisetum clandestinum), as well as common environmental weed species such as Wandering Dew (Tradescantia fluminensis), Rambling Dock (Acetosa sagittata), Moth Vine (Araujia sericifera).

Dominant Canopy Species: Casuarina cunninghamiana subsp. cunninghamiana, Eucalyptus elata, Eucalyptus botryoides x saligna, Angophora floribunda (20 m)

Small Tree Species: Acacia mearnsii, Acacia floribunda

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Dominant Shrub Species: Leptospermum emarginatum, Haloragis exaltata subsp. exaltata, Melicytus dentatus, Senecio linearifolius

Common Groundcover Species: Blechnum nudum, Adiantum aethiopicum, Oplismenus aemulus, Lomandra longifolia, Austrocynoglossum latifolium, Viola hederacea, Persicaria decipiens

Equivalent Map Units: Regional: F0W p30: South Coast River Flat Forest (Tozer et al. 2010) Biometric: River Peppermint - Rough-barked Apple - River Oak herb/grass riparian forest of coastal lowlands, southern Sydney Basin and South East Corner State: Eastern Riverine Forests (Keith 2006)

Conservation Status: This community has affinities to the state-listed threatened ecological community River-flat Eucalypt Forest considering the presence of this community on a coastal floodplain with diagnostic species including Rough-barked Apple (Angophora floribunda) and R iver Oak (casuarina cunninghamiana subsp. cunninghamiana).

The existing extant of this community is relatively small (8,400 ha) compared to other units, and has been subjected to substantial disturbance and clearing for agricultural with 50-65% of the pre-European extant estimated to remain (Tozer et al. 2010). It is moderately well represented in conservation reserves with <15% (1,600 ha) of the original pre-European extant estimated to occur in conservation reserves (Tozer et al. 2010).

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Appendix B Flora survey results Native floral species richness was relatively high within the naturally vegetated portions of the study area. As can be expected the grazed open pas ture areas of site were relatively low in native species diversity and r ichness due pr imarily to the long term effects of continued agriculture/grazing. A total of 330 flora species were recorded within the study area. This total comprised one c ycad species, one c onifer species, 14 s pecies of fern, 233 s pecies of dicotyledons and 80 s pecies of monocotyledons. Of the total species recorded, 49 species of introduced flora were identified, representing approximately 15 per cent of the total species.

i - introduced species

FAMILY Scientific Name Common Name Conifers

PINACEAE Pinus radiata Monterey Pine i

Cycads

ZAMIACEAE Macrozamia communis Burrawang

Ferns

ADIANTACEAE Adiantum aethiopicum Maidenhair Fern

ADIANTACEAE Adiantum hispidulum Rough Maidenhair

ADIANTACEAE Pellaea falcata var. falcata Sickle Fern

BLECHNACEAE Blechnum cartilagineum Gristle Fern

BLECHNACEAE Blechnum nudum Fishbone Water-fern

BLECHNACEAE Doodia aspera Prickly Rasp-fern

BLECHNACEAE Doodia caudata Small Rasp-fern

CYATHEACEAE Cyathea australis Rough Tree-fern

DAVALLIACEAE Davallia solida var. pyxidata Hare's-foor Fern

DENNSTAEDTIACEAE Calochlaena dubia False Bracken

DENNSTAEDTIACEAE Dennstaedtia davallioides Lacy Ground-fern

DENNSTAEDTIACEAE Pteridium esculentum Bracken

DRYOPTERIDACEAE Lastreopsis spp. Shield-fern

LINDSAEACEAE Lindsaea microphylla Lacy Wedge-fern

Flowering Plants - Dicotyledons

ACANTHACEAE Brunoniella pumilio Blue Trumpet

ACANTHACEAE Pseuderanthemum variable Pseuderanthemum

APHANOPETALACEAE Aphanopetalum resinosum Gum Vine

APIACEAE Centella asiatica Swamp Pennywort

APIACEAE Hydrocotyle laxiflora Stinking Pennywort

APIACEAE Hydrocotyle tripartita Tre-foil Pennywort

APIACEAE Platysace lanceolata Narrow-leaf Platysace

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FAMILY Scientific Name Common Name

APIACEAE Trachymene incisa subsp. incisa Native Carrot

APIACEAE Xanthosia atkinsoniana

APOCYNACEAE Araujia hortorum Moth Vine i

APOCYNACEAE Marsdenia rostrata Common Milk Vine

APOCYNACEAE Marsdenia suaveolens Scented Marsdenia

APOCYNACEAE Parsonsia straminea Common Silkpod

APOCYNACEAE Tylophora barbata Bearded Tylophora

ARALIACEAE Astrotricha latifolia Broad-leaf Star-hair

ARALIACEAE Polyscias sambucifolia Elderberry Panax

ASTERACEAE Aster subulatus Wild Aster i

ASTERACEAE Bedfordia arborescens Blanket Leaf

ASTERACEAE Bidens pilosa Cobblers Peg i

ASTERACEAE Calomeria amaranthoides Incense Plant

ASTERACEAE Cassinia aculeata Dollybush

ASTERACEAE Cassinia trinerva

ASTERACEAE Cirsium vulgare Spear Thistle i

ASTERACEAE Conyza spp. Fleabane i

ASTERACEAE Coronidium elatum subsp. elatum Tall Everlasting

ASTERACEAE Coronidium scorpioides Button Everlasting

ASTERACEAE Cotula australis Lawn Cotula

ASTERACEAE Gamochaeta sp. Cudweed i

ASTERACEAE Delairea odorata Cape Ivy i

ASTERACEAE Euchiton gymnocephalus

ASTERACEAE Euchiton sphaericus

ASTERACEAE Hypochaeris microcephala var. albiflora White Flatweed i

ASTERACEAE Hypochaeris radicata Catsear i

ASTERACEAE Lagenophora gracilis Slender Bottle-daisy

ASTERACEAE Lagenophora stipitata Bottle-daisy

ASTERACEAE Olearia tomentosa Hairy Daisy-bush

ASTERACEAE Ozothamnus argophyllus Spicy Everlasting

ASTERACEAE Ozothamnus diosmifolius Tall Paperdaisy

ASTERACEAE Senecio bipinnatisectus

ASTERACEAE Senecio hispidulus Hill Fireweed

ASTERACEAE Senecio linearifolius Fireweed Grounsel

ASTERACEAE Senecio madagascariensis Fireweed i

ASTERACEAE Senecio minimus Fireweed

ASTERACEAE Senecio quadridentatus Cotton Fireweed

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ASTERACEAE Senecio vagus subsp. vagus Saw Groundsel

ASTERACEAE Sigesbeckia orientalis Indian Weed

ASTERACEAE Sonchus oleraceus Common Sow-thistle i

ASTERACEAE Taraxacum officinale Dandelion

ASTERACEAE Vernonia cinerea var. cinerea Vernonia

ASTERACEAE Xerochrysum bracteatum Golden Everlasting

BIGNONIACEAE Pandorea pandorana Wonga Vine

BORAGINACEAE Austrocynoglossum latifolium

BORAGINACEAE Echium plantagineum Patterson’s Curse

BORAGINACEAE Ehretia acuminata var. acuminata Koda

BRASSICACEAE Lepidium bonariense Peppercress i

CALLITRICHIACEAE Callitriche stagnalis Common Starwort i

CAMPANULACEAE Wahlenbergia gracilis Sprawling Bluebell

CARYOPHYLLACEAE Polycarpon tetraphyllum Four-leaved Allseed i

CARYOPHYLLACEAE Stellaria flaccida Forest Starwort

CARYOPHYLLACEAE Stellaria media Common Chickweed i

CASUARINACEAE Allocasuarina littoralis Black She-oak

CASUARINACEAE Casuarina cunninghamiana River Oak

CHENOPODIACEAE Chenopodium album Fat Hen i

CHENOPODIACEAE Chenopodium ambrosioides Mexican Tea i

CLUSIACEAE Hypericum gramineum Narrow-leaf St. Johns Wort

CLUSIACEAE Hypericum japonicum Matted St. Johns Wort

CONVOLVULACEAE Calystegia marginata Forest Bindweed

CONVOLVULACEAE Dichondra repens Kidney Weed

CRASSULACEAE Crassula sieberiana Australian Stonecrop

DILLENIACEAE Hibbertia aspera Rough Guinea-flower

DILLENIACEAE Hibbertia dentata Twining Guinea-flower

DILLENIACEAE Hibbertia obtusifolia Hoary Guinea-flower

ELAEOCARPACEAE Elaeocarpus reticulatus Blueberry Ash

ELAEOCARPACEAE Tetratheca thymifolia Thyme-leaf Black-eyed Susan

ERICACEAE Leucopogon lanceolatus var. lanceolatus Lance-leaf Beard-heath

EUPHORBIACEAE Beyeria lasiocarpa

EUPHORBIACEAE Breynia oblongifolia Breynia

EUPHORBIACEAE Chamaesyce drummondii Caustic Weed

EUPHORBIACEAE Claoxylon australe Brittlewood

EUPHORBIACEAE Phyllanthus gunnii Blunt Spurge

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EUPHORBIACEAE Poranthera microphylla Small Poranthera

FABACEAE-FABOIDEAE Bossiaea obcordata Spiny Bossiaea

FABACEAE-FABOIDEAE Daviesia ulicifolia Gorse Bitter-pea

FABACEAE-FABOIDEAE Desmodium brachypodum Large Tick-trefoil

FABACEAE-FABOIDEAE Desmodium gunnii Slender Tick Trefoil

FABACEAE-FABOIDEAE Desmodium rhytidophyllum Rusty Tick-trefoil

FABACEAE-FABOIDEAE Desmodium varians Slender Tick-trefoil

FABACEAE-FABOIDEAE Glycine clandestina agg. Twining Glycine

FABACEAE-FABOIDEAE Glycine tabacina

FABACEAE-FABOIDEAE Hardenbergia violacea Purple Twining-pea

FABACEAE-FABOIDEAE Indigofera australis Native Indigo

FABACEAE-FABOIDEAE Kennedia rubicunda Dusky Coral Pea

FABACEAE-FABOIDEAE Medicago spp. Medic i

FABACEAE-FABOIDEAE Podolobium ilicifolium Prickly Shaggy-pea

FABACEAE-FABOIDEAE Pultenaea daphnoides Large-leaf Bush-pea

FABACEAE-FABOIDEAE Pultenaea paleacea Narrow-leaf Bush-pea

FABACEAE-FABOIDEAE Trifolium repens White Clover i

FABACEAE-MIMOSOIDEAE

Acacia falciformis Broad-leaf Hickory


Acacia floribunda Sally Wattle


Acacia implexa Hickory


Acacia irrorata subsp. irrorata Rough Green Wattle


Acacia linifolia Flax-leaf Wattle


Acacia longissima Long-leaf Wattle


Acacia maidenii


Acacia mearnsii South Coast Green Wattle


Acacia obtusifolia


Acacia subporosa River Wattle


Acacia terminalis Sunshine Wattle


Acacia ulicifolia Prickly Moses

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GENTIANACEAE Centaurium erythraea Common Centaury i

GENTIANACEAE Centaurium tenuiflorum i

GERANIACEAE Geranium homeanum Native Cranesbill

GERANIACEAE Geranium solanderi var. solanderi Native Cranesbill

GERANIACEAE Pelargonium inodorum

GOODENIACEAE Goodenia ovata Ovate Goodenia

GOODENIACEAE Scaevola aemula Fairy Fanflower

GOODENIACEAE Scaevola ramosissima Purple Fan-flower

HALORAGACEAE Gonocarpus teucrioides Raspwort

HALORAGACEAE Haloragis exalata subsp. exalata Square Raspwort t

LAMIACEAE Mentha pulegium Pennyroyal i

LAMIACEAE Plectranthus parviflorus Cockspur Flower

LAMIACEAE Prostanthera incisa

LAMIACEAE Prostanthera lasianthos Victorian Christmas Bush

LAMIACEAE Prunella vulgaris Self-heal i

LAMIACEAE Scutellaria mollis Dwarf Skullcap

LAURACEAE Cassytha pubescens Devils Twine

LOBELIACEAE Isotoma fluviatilis subsp. borealis Swamp Isotoma

LOBELIACEAE Pratia purpurascens White Root

LORANTHACEAE Amyema pendulum subsp. pendulum Pendulous Mistletoe

MALVACEAE Modiola caroliniana Red-flowered Mallow

MALVACEAE Sida rhombifolia Paddy’s Lucerne

MELIACEAE Toona ciliata Red Cedar

MELIACEAE Synoum glandulosum Scentless Rosewood

MENISPERMACEAE Sarcopetalum harveyanum Pearl Vine

MENISPERMACEAE Stephania japonica Snake Vine

MONIMIACEAE Wilkiea huegeliana Wilkiea

MORACEAE Ficus coronata Creek Sandpaper Fig

MYRSINACEAE Anagallis arvensis Pimpernel i

MYRSINACEAE Myrsine howittiana Brush Muttonwood

MYRTACEAE Angophora floribunda Rough-barked Apple

MYRTACEAE Backhousia myrtifolia Grey Myrtle

MYRTACEAE Eucalyptus agglomerata Blue-leaved Stringybark

MYRTACEAE Eucalyptus baueriana Blue Box

MYRTACEAE Eucalyptus bosistoana Coast Grey Box

MYRTACEAE Eucalyptus consideniana Yertchuk

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MYRTACEAE Eucalyptus cypellocarpa Monkey Gum

MYRTACEAE Eucalyptus elata River Peppermint

MYRTACEAE Eucalyptus globoidea White Stringybark

MYRTACEAE Eucalyptus longifolia Woollybutt

MYRTACEAE Eucalyptus muelleriana Yellow Stringybark

MYRTACEAE Eucalyptus radiata Narrow-leaved Peppermint

MYRTACEAE Eucalyptus saligna x botryoides

MYRTACEAE Eucalyptus sieberi Silvertop Ash

MYRTACEAE Eucalyptus tricarpa Mugga Ironbark

MYRTACEAE Leptospermum emarginatum Twin-flower Tea-tree

MYRTACEAE Sannantha pluriflora

MYRTACEAE Tristaniopsis laurina Water Gum

OLEACEAE Notelaea longifolia Large Mock Olive

OLEACEAE Notelaea venosa Smooth Mock Olive

OXALIDACEAE Oxalis perennans

PASSIFLORACEAE Passiflora herbertiana subsp. herbertiana Native Passion-fruit

PASSIFLORACEAE Passiflora edulis Passion-fruit i

PHYTOLACCACEAE Phytolacca octandra Inkweed i

PITTOSPORACEAE Billardiera scandens Apple-berry

PITTOSPORACEAE Bursaria spinosa Blackthorn

PITTOSPORACEAE Pittosporum multiflorum Orange Thorn

PITTOSPORACEAE Pittosporum revolutum Yellow Pittosporum

PITTOSPORACEAE Pittosporum undulatum Native Daphne

PLANTAGINACEAE Plantago debilis Slender Plantain

PLANTAGINACEAE Plantago lanceolata Plantain i

PLANTAGINACEAE Plantago major Large Plantain i

POLYGONACEAE Acetosa sagittata Rambling Dock i

POLYGONACEAE Acetosella vulgaris Sheep Sorrel i

POLYGONACEAE Persicaria decipiens Slender Knotweed

POLYGONACEAE Persicaria hydropiper Water Pepper

POLYGONACEAE Persicaria lapathifolia Pale Knotweed

POLYGONACEAE Persicaria praetermissa Knotweed

POLYGONACEAE Polygonum aviculare Variable-leaf Wireweed i

POLYGONACEAE Rumex brownii Swamp Dock

PROTEACEAE Banksia spinulosa var. spinulosa

PROTEACEAE Lomatia myricoides River Lomatia

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PROTEACEAE Persoonia linearis Narrow-leaf Geebung

RANUNCULACEAE Clematis aristata Toothed Clematis

RANUNCULACEAE Clematis glycinoides Entire-leaf Clematis

RANUNCULACEAE Ranunculus lappaceus Common Buttercup

RHAMNACEAE Pomaderris aspera Hazel Pomaderris

RHAMNACEAE Pomaderris discolor Pomaderris

RHAMNACEAE Pomaderris elliptica Pomaderris

RHAMNACEAE Pomaderris ferruginea

RHAMNACEAE Pomaderris lanigera Woolly Pomaderris

ROSACEAE Rubus fruticosus agg. Blackberry i

ROSACEAE Rubus moluccanus var. trilobus Molucca Bramble

ROSACEAE Rubus parviflorus Small-leaf Bramble

ROSACEAE Rubus rosifolius Rose-leaf Bramble

RUBIACEAE Galium binifolium

RUBIACEAE Galium propinquum Maori Bedstraw

RUBIACEAE Morinda jasminoides Morinda

RUBIACEAE Opercularia aspera Common Stinkweed

RUBIACEAE Opercularia diphylla Stinkweed

RUBIACEAE Opercularia hispida Hairy Stinkweed

RUBIACEAE Pomax umbellata Pomax

RUBIACEAE Psychotria loniceroides Hairy Psychotria

RUTACEAE Correa lawrenceana var. cordifolia Mountain Correa

RUTACEAE Correa reflexa Common Correa

RUTACEAE Philotheca myoporoides subsp. myoporoides

Long-leaf Wax Flower

RUTACEAE Zieria smithii Sandfly Zieria

SANTALACEAE Exocarpos cupressiformis Cherry Ballart

SANTALACEAE Exocarpos strictus Pale Ballart

SANTALACEAE Omphacomeria acerba

SANTALACEAE Santalum obtusifolium Sandalwood

SCROPHULARIACEAE Verbascum virgatum Twiggy Mullein i

SCROPHULARIACEAE Veronica calycina Common Speedwell

SCROPHULARIACEAE Veronica pleblia Trailing Speedwell

SOLANACEAE Physalis peruviana Cape Gooseberry i

SOLANACEAE Solanum americanum Glossy Nightshade i

SOLANACEAE Solanum aviculare Kangaroo Apple

SOLANACEAE Solanum chenopodioides Whitetip Nightshade i

155



SOLANACEAE Solanum nigrum Blackberry Nightshade i

SOLANACEAE Solanum prinophyllum Forest Nightshade

SOLANACEAE Solanum pseudocapsicum Jerusalem Cherry i

SOLANACEAE Solanum pungetium Eastern Nightshade

STERCULIACEAE Commersonia fraseri Brush Kurrajong

THEAPHRASTRACEAE Samolus valerandii Common Brookweed

THYMELEACEAE Pimelea linifolia subsp. linifolia Rice Flower

ULMACEAE Trema tomentosa var. aspera Native Peach

URTICACEAE Urtica incisa Scrub Stinging Nettle

VERBENACEAE Verbena bonariensis Purple Top i

VIOLACEAE Hybanthus monopetalus Slender Violet-bush

VIOLACEAE Melicytus dentatus Tree Violet

VIOLACEAE Viola hederacea Ivy-leaf Violet

VIOLACEAE Viola betonicifolia Native Violet

VITACEAE Cissus antarctica Water Vine

VITACEAE Cissus hypoglauca Five-leaf Water Vine

Flowering Plants - Monocotyledons

ANTHERICACEAE Arthropodium milleflorum Vanilla Lily

COMMELINACEAE Commelina cyanea Scurvy Weed

COMMELINACEAE Tradescantia albiflora Wandering Jew i

CYPERACEAE Carex appressa Tussock Tassel-sedge

CYPERACEAE Carex fascicularis Drooping Tassel-sedge

CYPERACEAE Carex inversa Knob Tassel-sedge

CYPERACEAE Gahnia melanocarpa Black-fruited Saw-sedge

CYPERACEAE Gahnia sieberiana Red-fruited Saw-sedge

CYPERACEAE Isolepis inundata Club-rush

CYPERACEAE Isolepis prolifera Club-rush

CYPERACEAE Lepidosperma elatius

CYPERACEAE Lepidosperma gunnii

CYPERACEAE Lepidosperma laterale Variable Sword-sedge

CYPERACEAE Lepidosperma urophorum Tussock Rapier-sedge

IRIDACEAE Libertia paniculata Branching Grass-flag

IRIDACEAE Patersonia sericea Silky Purple-flag

IRIDACEAE Sisyrinchium sp. A Scourweed i

JUNCACEAE Juncus planifolius Broadleaf Rush

JUNCACEAE Juncus prismatocarpus Branching Rush

JUNCACEAE Juncus usitatus Common Rush

156



JUNCAGINACEAE Triglochin procerum sens. st. Twisted Water Ribbons

LOMANDRACEAE Lomandra confertifolia subsp. rubiginosa Slender Mat-rush

LOMANDRACEAE Lomandra confertifolia subsp. similis Slender Mat-rush

LOMANDRACEAE Lomandra cylindrica

LOMANDRACEAE Lomandra filiformis subsp. filiformis Wattle Mat-rush

LOMANDRACEAE Lomandra glauca subsp. glauca Glaucous Mat-rush

LOMANDRACEAE Lomandra longifolia subsp. longifolia Spiny Mat-rush

LOMANDRACEAE Lomandra multiflora subsp. multiflora Many-flowered Mat-rush

LUZURIAGACEAE Eustrephus latifolius Wombat Berry

LUZURIAGACEAE Geitonoplesium cymosum Scrambling Lily

NAJADACEAE Najas tenuifolia Waternymph

ORCHIDACEAE Acianthus exsertus Giant Orchid

ORCHIDACEAE Cymbidium suave

ORCHIDACEAE Pterostylis grandiflora Cobra Greenhood

ORCHIDACEAE Thelymitra sp. Sun Orchid

PHORMIACEAE Dianella caerulea var. caerulea Leafy Blue Flax Lily

PHORMIACEAE Dianella caerulea var. producta Stemmed Blue Flax Lily

PHORMIACEAE Dianella tasmanica

POACEAE Aristida vagans Three-awned Spear Grass

POACEAE Austrodanthonia spp Wallaby Grass

POACEAE Austrodanthonia racemosa

POACEAE Austrostipa rudis Spear Grass

POACEAE Axonopus fissifolius Narrow-leaved Carpet Grass

i

POACEAE Cymbopogon refractus Barbed Wire Grass

POACEAE Cynodon dactylon Common Couch

POACEAE Dactylis glomerata Cocksfoot

POACEAE Dichelachne crinita Long-hair Plume Grass

POACEAE Dichelachne micrantha Short-hair Plume Grass

POACEAE Dichelachne parva

POACEAE Digitaria diffusa Open Summer-grass

POACEAE Digitaria sanguinalis Crab Grass i

POACEAE Echinopogon caespitosus Hedgehog Grass

POACEAE Echinopogon ovatus Hedgehog Grass

POACEAE Entolasia marginata Margined Panic

POACEAE Entolasia stricta Wiry Panic

POACEAE Eragrostis leptostachya Paddock Lovegrass

157



POACEAE Hemarthria uncinata var. uncinata Matgrass

POACEAE Imperata cylindrica Blady Grass

POACEAE Joycea pallida Red-anthered Wallaby Grass

POACEAE Lachnagrostis filiformis Blown Grass

POACEAE Microlaena stipoides var. stipoides Weeping Grass

POACEAE Notodanthonia longifolia Long-leaf Wallaby Grass

POACEAE Oplismenus aemulus Broad-leaf Beard-grass

POACEAE Oplismenus imbecillis Narrow-leaf Beard-grass

POACEAE Panicum simile Two-colour panic

POACEAE Paspalum dilatatum Paspalum i

POACEAE Pennisetum clandestinum Kikuyu i

POACEAE Phalaris aquatica Canary Grass i

POACEAE Plinthanthesis paradoxa Wiry Wallaby Grass

POACEAE Poa ensiformis Purple-sheathed Tussock-grass

POACEAE Poa labillardieri Tussock Grass

POACEAE Poa meionectes

POACEAE Setaria sp. Pigeon Grass i

POACEAE Sporobolus africanus Parramatta Grass i

POACEAE Themeda australis Kangaroo Grass

POTAMOGETONACEAE Potamogeton pectinatus Sago Pondweed

SMILACACEAE Smilax australis Lawyer Vine

STACKHOUSIACEAE Stackhousia monogyna Creamy Candles

UVULARIACEAE Schelhammera undulata Lilac Lily

XANTHORRHOEACEAE Xanthorrhoea concava? Grass-tree

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Appendix C Fauna survey data Mammals

A total of 15 native mammal species were recorded in the study area through a combination of trapping, visual observation and secondary indications (e.g. scats, tracks and diggings). Ground-dwelling small mammals were present in low abundance in the open forest habitat and only the Bush Rat was noted.

Macropods were uncommon, with only the Swamp Wallaby (Wallabia bicolour) noted. Bandicoot diggings, probably Long-nosed Bandicoot (Perameles nasuta) were particularly common in the open forest habitat on loamy soils. Other common species recorded include Common Brushtail Possum, while the Yellow-bellied Glider was found around wetter gullies and r iparian areas probably associated with the presence of hollow-bearing trees in these locations.

The use ultrasonic call recording identified a total of three microchiropteran bat species from this study and an additional 6 six species from the previous survey (NGH 2010).

Table C-1 Bat species recorded by ultrasonic call recording from current study

Species/Species Complex TSC Act No. of Confidence Level* Status calls

CL1 CL2 CL3

Eastern Forest Bat (Vespadelus sp.) -- 20 4 16

Vespadelus darlingtoni/V. regulus -- 39 5 34

Gould's Wattled Bat (Chalinolobus gouldii) -- 96 54 40 2

* Confidence Level: CL1 = Positive; CL2 = Probable, CL3 = Possible

All of these are known to roost in forest habitats, using tree hollows, spouts and crevices in trees as refuge, with the exception of the Eastern Horse-shoe Bat which is a cave-dweller. Four of the bat species detected are listed as vulnerable under the TSC Act: the Eastern False Pipistrelle (Falsistrellus tasmaniensis), Greater Broad-nosed Bat (Scoteanax rueppellii), Eastern Freetail-Bat (Mormopterus norfolkensis) and Eastern Bentwing-bat (Miniopterus schreibersii oceanensis). All species detected would likely use forested habitats across the entire study area for foraging.

Birds

A total of 49 bird species have been recorded in the study area from the two specialist surveys. A list of the species including their scientific and common name is provided below. This list represents a moderate species richness given the small area and degree of disturbance. The

159


diversity of species is a function of the availability of different habitats and the condition, and the presence of multiple food resources and s heltering microhabitats. The dominant bird groups noted included foliage insectivores also present were granivores, nectarivores, diurnal and nocturnal raptors, and aer ial foragers. Honeyeaters (Meliphagidae), Fantails/Flycatchers (Dicruridae) were particularly abundant. Common species included the Bell Miner, Lewins Honeyeater, Grey Fantail, Yellow Robin, Spotted Pardalote and Australian Magpie. Uncommon and threatened species included the Gang-Gang Cockatoo, Glossy Black-Cockatoo.

Reptiles and amphibians

The reptile diversity within the study area was dominated by skinks (Scincidae). A number of these species are generalists found in a variety of forest and woodland habitats where there is generally an adequate cover of trees, leaf litter and logs. This included the Weasel Skink which was widespread throughout all forested habitats and E astern Water Skink (Eulamprus quoyii) was restricted to creek habitats. No threatened reptile or amphibian was identified in the study area.

Only two frog species were identified within the study area, the Common Eastern Froglet and the Striped Marsh Frog. No threatened frog species was identified within the study area. Habitats for frogs are limited in the study are given the terrain and steep sloping ground which restricts any wet habitats to the flowing stream habitat of Dignams Creek and adjacent wet edges. Species which prefer shallow still water floodplains and soaks are expected to be absent.

List of fauna species recorded from the survey

V = Vulnerable species (NSW TSC ACT), Mi = Migratory listed species (EPBC Act)

Family / Scientific name Common name Status Current Study

NGH Environmental EPBC

Act TSC Act

BIRDS

Accipitridae

Accipiter novaehollandiae Grey Goshawk

Charadriidae

Vanellus miles Masked Lapwing

Columbidae

Leucosarcia melanoleuca Wonga Pigeon

Cacatuidae

Calyptorhynchus lathami Glossy Black-Cockatoo V

Calyptorhynchus funereus Yellow-tailed Black-

160




Act TSC Act

Cockatoo

Callocephalon fimbriatum Gang-gang Cockatoo V

Psittacidae

Alisterus scapularis Australian King-Parrot

Cuculidae

Cacomantis flabelliformis Fan-tailed Cuckoo

Chalcites lucidus Shining Bronze-Cuckoo

Podargidae

Podargus strigoides Tawny Frogmouth

Aegothelidae

Aegotheles cristatus Australian Owlet-nightjar

Apodidae

Hirundapus caudacutus White-throated Needletail Mi

Alcedinidae

Dacelo novaeguineae Laughing Kookaburra

Todiramphus sanctus Sacred Kingfisher

Menuridae

Menura novaehollandiae Superb Lyrebird

Climacteridae

Cormobates leucophaea White-throated Treecreeper

Climacteris erythrops Red-browed Treecreeper

Maluridae

Malurus cyaneus Superb Fairy-wren

Malurus lamberti Variegated Fairy-wren

Pardalotidae

Pardalotus punctatus Spotted Pardalote

Acanthizidae

Acanthiza lineata Striated Thornbill

Acanthiza pusilla Brown Thornbill

Sericornis frontalis White-browed Scrubwren

161




Act TSC Act

Meliphagidae

Myzomela sanguinolenta Scarlet Honeyeater

Acanthorhynchus tenuirostris Eastern Spinebill

Meliphaga lewinii Lewin's Honeyeater

Manorina melanophrys Bell Miner

Anthochaera carunculata Red Wattlebird

Philemon corniculatus Noisy Friarbird

Petroicidae

Eopsaltria australis Eastern Yellow Robin

Eupetidae

Psophodes olivaceus Eastern Whipbird

Pachycephalidae

Pachycephala pectoralis Golden Whistler

Pachycephala rufiventris Rufous Whistler

Colluricincla harmonica Grey Shrike-thrush

Dicruridae

Rhipidura albiscapa Grey Fantail

Rhipidura leucophrys Willie Wagtail

Myiagra inquieta Restless Flycatcher

Monarcha melanopsis Black-faced Monarch Mi

Campephagidae

Coracina novaehollandiae Black-faced Cuckoo-shrike

Coracina papuensis White-bellied Cuckoo-shrike

Oriolidae

Oriolus sagittatus Olive-backed Oriole

Artamidae

Strepera graculina Pied Currawong

Cracticus torquatus Grey Butcherbird

Gymnorhina tibicen Australian Magpie

Corvidae

162




Act TSC Act

Corvus coronoides Australian Raven

Ptilonorhynchidae

Ptilonorhynchus violaceus Satin Bowerbird

Estrildidae

Neochmia temporalis Red-browed Finch

Hirundinidae

Hirundo neoxena Welcome Swallow

Petrochelidon ariel Fairy Martin

MAMMALS

Peramelidae

Perameles nasuta Long-nosed Bandicoot

Vombatidae

Vombatus ursinus Common Wombat

Acrobatidae

Trichosurus vulpecula Common Brushtail Possum

Macropodidae

Wallabia bicolor Swamp Wallaby

Petauridae

Petaurus australis Yellow-bellied Glider V

Rhinolophidae

Rhinolophus megaphyllus Eastern Horseshoe-bat

Molossidae

Mormopterus norfolkensis Eastern Freetail-bat V

Vespertilionidae

Vespadelus darlingtoni Large Forest Bat

Miniopterus schreibersii oceanensis Eastern Bentwing-bat

V

Chalinolobus gouldii Gould's Wattled Bat

Scoteanax rueppellii Greater Broad-nosed Bat V

Scotorepens orion Eastern Broad-nosed Bat

163




Act TSC Act

Falsistrellus tasmaniensis Eastern False Pipistrelle V

Vespadelus vulturnus Little Forest Bat

Muridae

Rattus fuscipes Bush Rat

Rattus rattus Black Rat

Leporidae

Oryctolagus cuniculus Rabbit

AMPHIBIANS

Myobatrachidae

Limnodynastes peronii Brown-striped Frog

Crinia signifera Common Eastern Froglet

REPTILES

Agamidae

Physignathus lesueurii Eastern Water Dragon

Cheloidae

Chelodina longicollis Eastern Long-necked Turtle

Scincidae

Saproscincus mustelinus Weasel Skink

Eulamprus quoyii Eastern Water-skink

Tiliqua scincoides Eastern Blue-tongue

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Appendix D Aquatic survey data Aquatic macrophytes

Ten species of macrophytes were recorded during the surveys at five habitat survey sites, however none were rare or priority species (refer to Table D-1). Slender Knotweed (Persicaria decipiens) and Fl oating Clubrush (Isolepis fluitans) were the most abundant macrophytes, present in high densities at both sites. No aquatic weeds were observed within the study area.

Table D-1 Aquatic macrophytes recorded during field surveys

Common Name Scientific Name

AE1

(d/s

of

the

prop

osal

)

AE2

(u/s

of

the

prop

osal

)

AE3

AE4

AE5

Unknown Rush Eleocharis spp.

Chinese Water Chestnut Eleocharis dulcis

Common Rush Juncus spp.

Water Milfoil Myriophyllum

Swamp Lilly Ottelia ovalifolia

Slender Knotweed Persicaria decipiens

Floating Pondweed Potamogeton tricarinatus

Water Ribbons Triglochin procerum

Floating Clubrush Isolepis fluitans

Waterwort Elatine gratioloides

Water quality

Insitu water quality was monitored at two locations within Dignams Creek, one upstream of the proposal (Aquatic Site 1) and one dow nstream (Aquatic Site 2) (refer to Table D-2). Water quality was generally good with conductivity, pH and t urbidity within the ANZECC/ARMCANZ (2000) guidelines for the protection of aquatic ecosystems. Dissolved Oxygen was the only parameter that fell below the lower ANZECC/ARMCANZ (2000) guideline of 85 per cent saturation with a m ean concentration downstream of 79.43 ±0.13 per cent saturation and upstream of 77.73 ± 0.63 per cent saturation.

165


Table D-2 Water quality

Site Temp (°C)

Conductivi ty (µS/cm)

pH Dissolved Oxygen (mg/L)

Dissolved Oxygen (%sat)

Turbidit y (NTU)

OR P

Aquatic Site1

18.88 200 6.92 7.44 79.43 3.43 261. 67

Aquatic Site 2

19.54 200 6.92 7.17 77.73 1.93 231. 33

Outside the ANZECCC/ARMCANZ (2000) default trigger values for slightly disturbed aquatic ecosystems in upland rivers of South-East Australia.

Fish and aquatic reptiles

A total of 122 individuals from seven species of fish and aquatic reptiles were collected from the two aquatic survey sites sampled, one ups tream of the proposal (Aquatic Site1) and one downstream (Aquatic Site 2). Smelt was the most abundant fish recorded with over 86 individuals present. C ommon Jollytail & Flathead Gudgeon were also recorded in higher abundances with 11 and 13 i ndividuals recorded respectively. Table D-3 provides details of the aquatic fauna captured during field surveys.

Table D-3 Fish captured during field surveys

Common Name Scientific Name Aquatic Site 1 Aquatic Site 2

Short finned Eel Anguilla austalis 0 3

Freshwater catfish Tandanus tandanus 0 1

Australian Smelt Retropinna semoni >50 36

Common Jollytail Galaxias maculatus 7 4

Striped Gudgeon Gobiomorphus australis 3 2

Flathead Gudgeon Philypnodon grandiceps 8 5

Eastern Long-necked Turtle Chelodina longicollis 2 1

Macroinvertebrates

Twenty-eight macroinvertebrate families were observed within edge and r iffle habitats within Dignams Creek (refer to Table D-4). AUSRIVAS observed to expected ratios (OE50 score) calculated for each site indicated that the edge habitats within Dignams Creek sites were in good ecological condition with both sites receiving an O E50 scores of 0.86, falling within Band A -reference condition. The riffle habitat was in poorer ecological condition with a lower OE50 score (0.45) resulting in an AUSRIVAS Band B - Significantly impaired, indicating that fewer macroinvertebrates were observed than would be collected if the site was in reference condition.

166


Table D-4 Macroinvertebrates collected within Dignams Creek

Family AE1 (Edge Habitat) AE1 (Riffle Habitat) AE2 (Edge Habitat)

Acarina 3 9

Amphipoda 3

Atyidae 2 2 2

Baetidae 9 4

Chironominae 6 2 4

Copepoda 3 1 2

Corixidae 3 5

Culicidae 3

Ceratopogonidae 2 1 2

Coenagrionidae 1

Dytiscidae 2 2 1

Gerridae 3 1

Gyrinidae 11 7

Gripopterygidae 2 9 1

Gomphidae 2 1

Hydrophilidae 1 3

Hydroptilidae 1

Leptoceridae 2 1 2

Mesoveliidae 2

Leptophlebiidae 8 2 5

Notonemouridae 4 2

Hydropsychidae 13

Orthocladiinae 9

Oligochaeta 1

Odonata 2 1

Philopotamidae 5

Notonectidae 7 5

Simuliidae 2

167


Appendix E Threatened subject species assessment The following assessment identifies the list of threatened flora and fauna species recorded from a 10 k m radius of the proposal and compares the preferred habitat of these species with the habitats identified in the study area to make an assessment of the likelihood of the species being present in the proposal study area (ie subject species). The criteria used in the assessment are detailed below.

Likelihood of Occurrence

Criteria

Unlikely Species highly restricted to certain geographical areas not within the proposal area

Specific habitat requirements are not present in the study area

Low Species not recorded during field surveys and fit one or more of the following criteria:

Have not been recorded previously in the study area/surrounds and for which the study area is beyond the current distribution range

Use specific habitats or resources not present in the study area

Are a non-cryptic perennial flora species that were specifically targeted by surveys and not recorded

Moderate Species not recorded during the field surveys that fit one or more of the following criteria:

Have infrequently been recorded previously in the study area/surrounds

Use specific habitats or resources present in the study area but in a poor or modified condition

Are unlikely to maintain sedentary populations, however may seasonally use resources within the study area opportunistically or during migration

Are cryptic flowering flora species that were not seasonally targeted by surveys and that have not been recorded

High Species recorded during the field surveys or species not recorded that fit one or more of the following criteria:

Have frequently been recorded previously in the study area/surrounds

Use habitat types or resources that are present in the study area that are abundance and/or in good condition within the study area

Are known or likely to maintain resident populations surrounding the study area

Are known or likely to visit the site during regular seasonal movements or migration

168


Table E-1: Distribution and habitat requirements of potentially occurring threatened flora species

Species Status Distribution and Habitat Requirements Likelihood of occurrence

Broad Preferred Habitat Type

EPB

CA

ct

TSC

Act

RoT

AP

Acacia georgensis (Bega Wattle) V V 2VCi Only occurs in the far South East of NSW with known sites at Kianinny Bay in Bournda

National Park, on Dr George Mountain, Wadbilliga National Park and in Bemboka and Coolangubra Sections (one location on cliffs above the Towamba River) of the South East Forests National Park. Typically occurs on well-drained, shallow soils at sites with considerable exposed rock. The sites where it is found represent a range of different environments with correspondingly varied vegetation; in general, other tree species are uncommon but can include Veined Olive (Notelaea venosa), Hickory Wattle (Acacia implexa), Forest Red-gum (Eucalyptus tereticornis), Woolybutt (E. longifolia), Bega Mallee (E. spectatrix) and Gully Gum (E. smithii).

Low Dry sclerophyll forest

Aldrovanda vesiculosa Waterwheel Plant

- E - More commonly found in northern Australia and tropical regions of Asia and Africa. Known in NSW only from wetlands in the Moruya area and the Evans Head area in the north-east. Found in near-coastal shallow freshwater ponds and w etlands poor in lime and rich in organic matter.

Low Freshwater wetlands

Budawangia gnidioides (Budawangs Cliff-heath)

V V 2VC-t Has only been recorded in the Northern Budawang Range west of Ulladulla. Grows in skeletal soil in sandstone crevices or on sandy ledges beneath cliffs, on the margins of open forest and heathland.

Low Dry sclerophyll forest and heathland

Caladenia tessellata (Thick-lip Spider Orchid)

V E 3VCa Occurs in the Sydney area, Wyong, Ulladulla and Braidwood. Populations in Kiama and Queanbeyan are presumed extinct. Has been recorded in the Huskisson area in the 1930s. Generally found in grassy sclerophyll woodland on clay loam or sandy soils, however the population near Braidwood is in low woodland with stony soil.

Moderate Grassy woodlands and sclerophyll forest

Correa baeuerlenii (Chef’s Cap Correa)

V V 3VCi Has been recorded between Nelligen (on Nelligen Creek and the Buckenbowra River) and Mimosa Rocks National Park. Occurs in riparian sites within forests of various eucalypts, including Silvertop Ash (Eucalyptus sieberi), Yellow Stringybark (E. muelleriana), Blue-leafed Stringybark (E. agglomerata) and Spotted Gum (Corymbia

Moderate Dry sclerophyll forest and heathland

169




EPB

CA

ct

TSC

Act

RoT

AP

maculata) or she-oak woodland. It may also be found in near-coastal rocky sites.

Cryptostylis hunteriana (Leafless Tongue Orchid)

V V 3VC- Recorded from as far north as Gibraltar Range National Park south into Victoria around the coast as far as Orbost. It is known historically from a number of localities on the NSW south coast and has been observed in recent years at many sites between Batemans Bay and Nowra although it is uncommon at all sites. Also recorded at Nelson Bay, Wyee, Washpool National Park, Nowendoc State Forest, Ku-Ring-Gai Chase National Park, Ben Boyd National Park. Does not appear to have well defined habitat preferences and is known from a range of communities, including swamp-heath and woodland. The larger populations typically occur in woodland dominated by Scribbly Gum (Eucalyptus sclerophylla), Silvertop Ash (E. sieberi), Red Bloodwood (Corymbia gummifera) and Black She-oak (Allocasuarina littoralis). Seems to prefer open areas in the understorey of this community and is often found in association with the Large Tongue Orchid (Cryptostylis subulata) and the Tartan Tongue Orchid (Cryptostylis erecta).

Moderate Swampy heath and woodland areas

Galium australe (Tangled Bedstraw) V V -

Widespread in Victoria and is also found in South Australia and Tasmania. Once regarded as presumed extinct in NSW, this species is now known from the Towamba Valley near Bega, Lake Yarrunga near Kangaroo Valley, Cullendulla Creek Nature Reserve near Batemans Bay, Conjola National Park, Swan Lake near Swanhaven, and the Big Hole in Deua National Park. It was recorded historically from the Clyde River near Batemans Bay and the Mongarlowe area near Braidwood. The species also occurs beside Lake Windemere in the Australian Capital Territory at Jervis Bay. In NSW it is found in moist gullies of tall forest including Forest Red Gum (Eucalyptus tereticornis) forest, coastal Banksia shrubland, and Allocasuarina nana heathland. In other States the species is found in a range of near-coastal habitats, including sand dunes, sand spits, shrubland and woodland.

Low Dry and wet sclerophyll forest and heathland

Genoplesium vernal (East Lynee Midge Orchid)

- V 3RCi Currently known from only a narrow belt, approximately 12 kilometres wide, of predominantly Dry Sclerophyll Forest from 17 kilometres south of Batemans Bay to 24 kilometres north of Ulladulla. Grows in ‘poorer’ dry sclerophyll woodland and forest, confined to areas with good drainage and shallow, low fertility soils.


Haloragis exaltata subsp. exaltata

V V - Occurs in 4 widely scattered localities in eastern NSW. It is present in the study area, where it is scattered along the bed and banks of Dignams Creek. It was not found on any

Present Riparian areas

170




EPB

CA

ct

TSC

Act

RoT

AP

(Square Raspwort) tributary gullies. Grows in a range of habitats, usually close to water and often disturbed. A preliminary determination has been made to delist the species in NSW.

Lysimachia vulgaris var. davurica (Yellow Loosestrife)

E - - Only known from Wingecarribee Swamp, the Boro area near Braidwood and the Bega River Valley. The NSW populations are in disparate habitat: extensive wetland on peaty soils, riparian wetland vegetation and pasture on a dairy farm.

Moderate Wetlands, riparian areas and cleared pasture.

Monotaxis macrophylla (Large-leaf Monotaxis)

- E 2VCi Recorded from several highly disjunct populations in NSW: eastern edge of Deua NP (west of Moruya), Bemboka portion of South East Forests National Park, Cobar area (Hermitage Plains), the Tenterfield area, and Woodenbong (near the Queensland border). It is also in Queensland. A recent record from the eastern spur of the Nandewar Range is in the Namoi catchment. Within NSW, the species has not been found in the absence of fire. There is a great diversity in the associated vegetation within NSW (less though in Queensland), encompassing coastal heath, arid shrubland, forests and montane heath from almost sea level to 1300 metre altitude.

Low Heath, shrubland and forests

Persicaria elatior (Tall Knotweed)

V V 3V In northern NSW it is known from Raymond Terrace and the Grafton area. This species normally grows in damp places, especially beside streams and lakes. Occasionally in swamp forest or associated with disturbance.

Moderate Wetlands and riparian areas

Pomaderris bodalla (Bodalla Pomaderris) V V

Currently known to occur on the south coast between Bodalla and Merimbula, and in the upper Hunter Valley near Muswellbrook. There are ten populations currently known, and a further two imprecisely described locations from which the species was collected approximately 40 years ago. The majority of populations are small with seven of the populations having estimates of less than a hundred plants each. All populations have locally restricted distributions. On the south coast it occurs in moist open forest along sheltered gullies or along stream banks.

Moderate Wet Sclerophyll Forest and riparian areas

Pultenaea pedunculata (Matted Bush-pea)

- V - Widespread in Victoria, Tasmania, and south-eastern South Australia, However in NSW it is represented by just three disjunct populations on the Cumberland Plains in Sydney, the coast between Tathra and Bermagui and the Windellama area south of Goulburn. NSW populations are generally among woodland vegetation but plants have also been found


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AP

on road batters and coastal cliffs. It is largely confined to loamy soils in dry gullies in populations in the Windellama area.

Thesium australe (Austral Toadflax)

V V 3VCi +

Austral Toad-flax is found in very small populations scattered across eastern NSW, along the coast, and from the Northern to Southern Tablelands. It is also found in Tasmania and Queensland and in eastern Asia. Occurs in grassland or grassy woodland. Often found in damp sites in association with Kangaroo Grass (Themeda australis). A root parasite that takes water and some nutrient from other plants, especially Kangaroo Grass.

Low Grassland and grassy woodland

Wilsonia backhousei (Round-leaf wilsonia) - V -

Found on the coast between Mimosa Rocks National Park and Wamberal north of Sydney. It grows in all southern states. This is a species of the margins of salt marshes and lakes, both coastal and inland.

Low Saltmarsh

Zieria tuberculata (Warty Zieria) V V -

Occurs in the Mt Dromedary and Tilba Tilba area. Grows in heath amongst rocky outcrops on rainforest edges and in tall forest and shrubland.

Low Dry and wet sclerophyll forest, heathland and rainforest

Sources: * Distribution and habitat requirement information adapted from the Department of Environment and Climate Change (updated 2005) Threatened Species Website (http://www.threatenedspecies.environment.nsw.gov.au/tsprofile/browse_allspecies.aspx)

+ Rare or Threatened Australian Plants (RoTAP) Briggs, JD; Leigh, JH [1979] (1996). Rare or Threatened Australian Plants, Fourth Edition, CSIRO Publishing

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http://www.threatenedspecies.environment.nsw.gov.au/tsprofile/browse_allspecies.aspx


Table E-2: Threatened terrestrial and aquatic fauna, distribution and habitat requirements and potential to occur in the study area

Species Status Distribution and habitat requirements* Likelihood of occurrence

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Eastern Pygmy Possum (Cercartetus nanus ) V Found in a broad range of habitats from rainforest through to wet and dry sclerophyll forest and woodland to

heath, but in most areas woodlands and heath appear to be preferred. Low

Large-eared Pied Bat

(Chalinolobus dwyeri)

V V Forages over a broad range of open forest and woodland habitats, this species is a cave roosting bat which favours sandstone escarpment habitats for roosting, in the form of shallow overhangs, crevices and caves.

Moderate

White-footed Dunnart (Sminthopsis leucopus)

V Found in a range of different habitats across its distribution, including coastal dune vegetation, coastal forest, tussock grassland and sedgeland, heathland, woodland and forest.

In NSW, the species seems to favour vegetation communities with an open understorey structure.

Moderate

Spotted-tailed Quoll

(Dasyurus maculatus)

E V Wet and dry sclerophyll forests and rainforests, and adjacent open agricultural areas. Generally associated large expansive areas of habitat to sustain territory size.

High

Eastern False Pipistrelle

(Falsistrellus tasmaniensis)

V Occurs in a variety of open forest and woodland habitats, where hollow-bearing trees are present and required for roosting, may forage in younger regrowth and modified environments.

Present

Southern Brown Bandicoot

(Isoodon o. obesulus)

E E Typically associated with coastal heaths or open forest habitats with a he athy understorey on s andy soils. South from Hawkesbury River to Victoria

Unlikely

Eastern Bent-wing Bat

(Miniopterus schreibersii oceanensis)

V Forages in a variety of habitat types including, dry sclerophyll forests and woodlands, as well as cleared and modified urban environments, a cave roosting species requiring caves and artificial tunnels for breeding and roosting.

Present

Eastern Freetail Bat

(Mormopterus norfolkensis)

V Occur in dry sclerophyll forest and woodland east of the Great Dividing Range. Roosts mainly in tree hollows but will also roost under bark or in man-made structures.

Present

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Southern Myotis

(Myotis macropus)

V Generally roost in groups close to water in caves, mine shafts, hollow-bearing trees, storm water channels, buildings, under bridges and in dense foliage. Forages over streams and pools catching insects and small fish.

Moderate

Yellow-bellied Glider

(Petaurus australis)

V Tall open forest habitats, favours mature wet sclerophyll forest and dense gullies. Present

Squirrel Glider

(Petaurus norfolcensis)

V Forest and woodland habitats, particularly areas with a diversity of eucalypt species in the canopy and other suitable food resources (shrubs and small trees). Requires tree hollows for denning.

Unlikely

Brush-tailed Phascogale (Phascogale tapoatafa)

V Prefer dry sclerophyll open forest with sparse groundcover of herbs, grasses, shrubs or leaf litter. Also inhabit heath, swamps, rainforest and wet sclerophyll forest.

Moderate

Brush-tailed Rock Wallaby

(Petrogale penicillata)

E E Open forest habitats on steep terrain with exposed rocks, rock overhangs and platforms. Unlikely

Koala

(Phascolarctos cinereus)

V V Open forests and woodlands with favoured food tree species, which in the study area includes a number of supplementary species for the south coast region as reported in DEC (2009) such as White Stringybark (E. globoidea), Yellow Stringybark (E. muelleriana), Blue-leaved Stringybark (E. agglomerata) .

High

Long-nosed Potoroo

(Potorous t. tridactylus)

V V Inhabits coastal heaths and dry and wet sclerophyll forests. Dense understorey with occasional open areas is an essential part of habitat, and may consist of grass-trees, sedges, ferns or heath, or of low shrubs of tea-trees or melaleucas. A sandy loam soil is also a common feature.

Moderate

Grey-headed Flying-fox

(Pteropus poliocephalus)

V V Occur in subtropical and temperate rainforests, tall sclerophyll forests and woodlands, heaths and swamps as well as urban gardens and cultivated fruit crops.

Moderate

Smoky Mouse

(Psuedomys fumeus)

E CE The Smoky Mouse appears to prefer heath habitat on ridge tops and slopes in sclerophyll forest, heathland and open-forest from the coast (in Victoria) to sub-alpine regions of up to 1800 metres, but sometimes occurs in ferny gullies.

Unlikely

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Nesting burrows have been f ound in rocky localities among tree roots and un der the skirts of Grass Trees Xanthorrhoea spp.

New Holland Mouse

(Psuedomys novaehollandiae)

E - The New Holland Mouse is known to inhabit open heathlands, open woodlands with a heathland understorey, and vegetated sand dunes.

Low

Yellow-bellied Sheathtail-bat

(Saccolaimus flaviventris)

- V Forages in most habitats across its wide range, with and without trees; appears to defend an aer ial territory. Roost in tree hollows and buildings.

High

Golden-tipped Bat (Kerivoula papuensis)

Rainforests and wet gullies Low

Greater Broad-nosed Bat

(Scoteanax rueppellii)

- V Inhabits a broad range of forest and woodland habitats, including adjacent cleared lands. Present

Square-tailed Kite (Lophoictinia isura)

- V Found in a variety of timbered habitats including dry woodlands and open forests. Shows a particular preference for timbered watercourses.

Moderate

Spotted Harrier (Circus assimulis)

- V Occurs in grassy open woodland including Acacia and mallee remnants, inland riparian woodland, grassland and shrub steppe. It is found most commonly in native grassland, but also occurs in agricultural land, foraging over open habitats including edges of inland wetlands.

Unlikely

Pied Oystercatcher (Haematopus longirostris)

- E It is thinly scattered along the NSW coast where it favours marine littoral habitats. It occupies muddy, sandy, rocky estuaries, open beaches and intertidal mudflats and sandbanks.

Unlikely

Osprey (Pandion haliaetus) Mi V Occur in coastal areas at the mouth of large rivers, lagoons and lakes and may move upstream to feed on fish. Low

Little Tern (Sterna albifrons) Mi E Prefers sheltered habitats on the coast and may occur in sea harbours, inlets and rivers. Nests in colonies on low dunes and beaches.

Unlikely

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Olive Whistler (Pachycephala olivace)

- V Populations occur in north and south of NSW. Inhabits dense wet forests from Illawarra to Victoria along the east coast.

Low

Regent Honeyeater

(Xanthomyza phrygia)

E, Mi CE A nomadic species typically associated with forest and woodland habitats with the presence of suitable foraging species such as Yellow Box and Red Ironbark

Low

Swift Parrot

(Lathamus discolor)

E, Mi E On the mainland they occur in areas where eucalypts are flowering profusely or where there are abundant lerp (from sap-sucking bugs) infestations. Favoured feed trees include winter flowering species such as Swamp Mahogany Eucalyptus robusta, Spotted Gum Corymbia maculata, Red Bloodwood C. gummifera, Mugga Ironbark E. sideroxylon, and White Box E. albens.

Low

Orange-bellied Parrot

(Neophema chrysogaster)

CE CE Breeds in the south-west of Tasmania and migrates in autumn to spend the winter on the mainland coast of south-eastern South Australia and southern Victoria. There are occasional reports from NSW, with the most recent records from Shellharbour and Maroubra in May 2003. Typical winter habitat is saltmarsh and strandline/foredune vegetation communities either on coastlines or coastal lagoons. Birds forage in low samphire herbland or taller coastal shrubland.

Unlikely

Gang-gang Cockatoo

(Callocephalon fimbriatum)

- V Moist and tall open forests, particularly in steep topographic areas. Numerous records in the study area. High

Glossy Black-Cockatoo

(Calyptorhynchus lathami)

- V Open forest habitats with She-oak species (Allocasuarina spp.) required for food. High

Brown Treecreeper

(Climacteris picumnus)

- V Woodland bird species, favour dry sclerophyll forests and woodlands, generally with a sparse understorey, grassy areas and mature hollow-bearing trees.

Low

Hooded Robin

(Melanodryas cucullata)

- V Woodland bird species, favour dry sclerophyll forests and woodlands, generally with a sparse understorey, grassy areas and logs.

Low

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Black-chinned Honeyeater

(Melithreptus g. gularis)

- V Woodland bird species, favour dry sclerophyll forests and woodlands, generally with a sparse understorey, grassy areas and logs.

Low

Barking Owl

(Ninox connivens)

V Forest and woodland habitats, particularly drier western slopes and riverine areas, hunts for birds and small mammals.

Moderate

Powerful Owl

(Ninox strenua)

V Open forests with dense wet gullies and creek areas, requires large mature trees with hollows for breeding and dense areas of vegetation for prey and roosting

High

Sooty Owl

(Tyto tenebricosa)

V Occurs in rainforest, including dry rainforest, subtropical and w arm temperate rainforest, as well as moist eucalypt forests.

Moderate

Masked Owl

(Tyto novaehollandiae)

V Lives in dry eucalypt forests and woodlands from sea level to 1100 m. Moderate

Blue-billed Duck

(Oxyura australis)

V Prefers deep water in large permanent wetlands and swamps with dense aquatic vegetation. Unlikely

Pink Robin

(Petroica rodinogaster)

V In NSW this species is generally found in the south-east as far north as Bombala. It breeds during spring-summer and disperses to more open habitats in winter north to the central coast. Inhabits rainforest and moist tall open eucalypt forest, particularly densely vegetated gullies.

Moderate

Australian Painted Snipe

(Rostratula australis)

E Prefers fringes of swamps, dams and nearby marshy areas where there is a cover of grasses, lignum, low scrub or open timber.

Unlikely

Rosenberg's Goanna

(Varanus rosenbergi)

- V Occurs on the Sydney Sandstone in Wollemi National Park to the north-west of Sydney, in the Goulburn and ACT regions and near Cooma in the south. There are records from the South West Slopes near Khancoban and Tooma River. Also occurs in South Australia and Western Australia. Found in heath, open forest and woodland.

Low

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Broad-headed Snake

(Hoplocephalus bungaroides)

V V Shelters in rock crevices and under flat sandstone rocks on exposed cliff edges during autumn, winter and spring. Moves from the sandstone rocks to shelters in hollows in large trees within 200 metre of escarpments in summer.

Unlikely

Giant Burrowing Frog (Helioporus australicus)

V V Found in a range of forest types on the coast and adjacent ranges including heaths, woodlands and open forests. The Giant Burrowing Frog will travel several hundred metres to creeks to breed. It has also been recorded in roadside drains and near slow-flowing creeks and pools with fringing fern and sedge vegetation. Breeds summer and autumn in borrows in creek banks, favouring deep loamy soils.

Moderate

Green and Golden Bell Frog (Litoria aurea)

V E Inhabits marshes, dams and streams, particularly those containing bullrushes (Typha spp.) or spikerushes (Eleocharis spp.). Optimum habitat includes water-bodies that are unshaded, free of predatory fish such as Plague Minnow (Gambusia holbrooki), have a grassy area nearby and diurnal sheltering sites available. Some sites, particularly in the Greater Sydney region occur in highly disturbed areas.

Unlikely

Stuttering Frog

(Mixophyes balbus)

V E Permanent streams in moist and wet sclerophyll forests Moderate

Little John’s Tree Frog

(Litoria littlejohni)

V V It occurs along permanent rocky streams with thick fringing vegetation associated with eucalypt woodlands and heaths among sandstone outcrops.

Low

Australian Grayling (Prototroctes maraena)

V - The Australian Grayling occurs in south-eastern Australia, in coastal rivers and streams in New South Wales, Victoria and Tasmania. On the mainland it occurs from the Shoalhaven River (NSW) south and west to the Hopkins River system (Vic).

The Australian Grayling is a diadromous species, migrating between rivers, their estuaries and coastal seas, so relies on free access to a range of freshwater, estuarine and marine habitats for its survival. Australian Grayling spend most of their lives in freshwater, inhabiting rivers and streams, usually in cool, clear waters with a gravel substrate and alternating pool and riffle zones but can also occur in turbid water. The species can penetrate well inland, and has been reported from over 100 kilometre upstream from the sea. Larvae and juveniles inhabit

Low

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estuaries and coastal seas, and there appears to be an obligatory marine stage, although their precise habitat requirements are not known.

Australian Grayling is not listed under NSW legislation (FM Act).

Table E-3: Potential occurrence of migratory species (EPBC Act)

Common Name Species Preferred habitat Likelihood of occurrence

Black-faced Monarch Monarcha melanopsis Rainforests, eucalypt forests and coastal scrubs Moderate

Cattle Egret Ardea ibis Grasslands, woodlands and wetlands, and is not common in arid areas. It also uses pastures and croplands, especially where drainage is poor. Often seen with cattle.

High

Fork-tailed Swift Apus pacificus The species breeds in Asia and migrate to Australia in the summer from which they spend their entire life-cycle on the wing, hunting, resting and sleeping.

High

Great Egret Ardea alba Prefers shallow water, particularly when flowing, but may be seen on any watered area, including damp grasslands.

High

Latham’s snipe Galliago hardwickii Wetlands, wet meadows, flooded grassy paddocks, open grassland and drainage areas Moderate

Orange-bellied Parrot Neophema chrysogaster Spends winter mostly within 3 kilometre of the coast in sheltered coastal habitats including bays, lagoons, estuaries, coastal dunes and saltmarshes.

Unlikely

Osprey Pandion cristatus Occurs in littoral and coastal habitats and terrestrial wetlands of tropical and temperate Australia and offshore islands.

Low

Painted snipe Rostratula australis Wetlands, reedlands, marshes and swamps Unlikely

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Common Name Species Preferred habitat Likelihood of occurrence

Rufous Fantail Rhipidura rufifrons Predominantly rainforest and forests Moderate

Rainbow Bee-eater Merops ornatus Predominantly woodland and timbered plains Moderate

Regent Honeyeater Xanthomyza phrygia A nomadic species typically associated with forest and woodland habitats with the presence of suitable foraging species such as Yellow Box and Red Ironbark

Low

Satin Flycatcher Myiagra cyanoleuca Predominantly forests, in particular thick vegetation in gullies Moderate

Spectacled Monarch Monarcha trivirgatus Prefers a thick understorey in rainforests, wet gullies and waterside vegetation, as well as mangroves. Moderate

White-bellied Sea Eagle Haliaeetus leucogaster Predominantly ocean shores and estuaries, occasionally inland rivers and streams. Moderate

White-throated Needletail

Hirundapus caudacutus An aerial foraging species which occupies a range of habitats from open modified landscapes to woodland and forest.

Moderate

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Appendix F Assessments of Significance F.1 Environmental Planning and Assessment Act 1995 (S.5a) Threatened Ecological Communities – River-flat Eucalypt Forest on CoastalFloodplains (a) In the case of a threatened species, whether the action proposed is likely to have an adverse effect on the life cycle of the species such that a viable local population of the species is likely to be placed at risk of extinction.

No consideration under this part of the assessment is required.

(b) In the case of an endangered population, whether the action proposed is likely to have an adverse effect on the life cycle of the species that constitutes the endangered population such that a viable local population of the species is likely to be placed at risk of extinction.


(c) In the case of an endangered ecological community, whether the action proposed:

is likely to have an adverse effect on the extent of the ecological community such that its local occurrence is likely to be placed at risk of extinction, or

is likely to substantially and adversely modify the composition of the ecological community such that its local occurrence is likely to be placed at risk of extinction.

Direct impacts to the threatened ecological community (Map Unit 5) would involve approximately 0.2 hectares comprising approximately 0.1 hectares of moderate condition vegetation along Dignams Creek comprising a thin strip of riparian vegetation at the proposed crossing site and approximately 0.1 hectares of high condition vegetation along Blind Creek at the intersection with Dignams Creek Road.

There is approximately 76,767 hectares of vegetation consistent with River-flat Eucalypt Forest on Coastal Floodplains within 10 kilometres of the proposal (Tozer et al. 2010). The potential impacts for the proposed upgrade represent less than 0.002% of this vegetation type in the region.

The presence of this vegetation community in the study area is highly fragmented and disturbed as a result of the long history of agricultural activities such as clearing, pasture improvement and grazing. As a consequence of this the vegetation supports a high density of exotic plant species and has a reduced structural and species diversity.

Considering these factors and with the small area of vegetation that would actually be cleared in relation to the extent of the community in the local area it is considered unlikely that the loss or disturbance would adversely affect the remainder of the community in this location or lead to local extinction.

(d) In relation to the habitat of a threatened species, population or ecological community:

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the extent to which habitat is likely to be removed or modified as a result of the action proposed, and

whether an area of habitat is likely to become fragmented or isolated from other areas of habitat as a result of the proposed action; and

the importance of the habitat to be removed, modified fragmented or isolated to the long-term survival of the species, population or ecological community in the locality,

Direct impacts to the threatened ecological community (Map Unit 5) would involve approximately 0.2 hectares comprising approximately 0.1 hectares of moderate condition vegetation along Dignams Creek comprising a thin strip of riparian vegetation at the proposed crossing site and approximately 0.1 hectares of high condition vegetation along Blind Creek at the intersection with Dignams Creek Road.

The presence of this vegetation community in the study area is highly fragmented and disturbed as a result of the long history of agricultural activities such as clearing, pasture improvement and grazing. There would be limited further fragmentation as a result of clearing a 30-40 metre wide area for the proposal corridor and br idge crossing. Connectivity would be m aintained along this riparian zone with the regeneration of vegetation surrounding and beneath the proposed bridge structure over Dignams Creek. Further revegetation is to be conducted post-construction as part of the CEMP.

As discussed this vegetation community at the site is highly fragmented and h ighly disturbed from the past land-use with a high density of weeds and diminished structural and species diversity. This being considered the habitat to be removed is not considered important for the long-term survival of this TEC.

(e) whether the action proposed is likely to have an adverse effect on critical habitat (either directly or indirectly).

Critical habitat has not been declared for River-flat Eucalypt Forest.

(f) whether the action proposed is consistent with the objectives or actions of a recovery plan or threatened abatement plan

There is no recovery plan for River-flat Eucalypt Forest

(g) whether the action proposed constitutes or is part of a threatening process or is likely to result in the operation of, or increase the impact of, a key threatening process.

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Threatening Process

DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 0.2 hectares of River-flat Eucalypt Forest. The proposed upgrade has been designed to minimise vegetation clearing where possible and minimise potential impacts to areas of high condition River-flat Eucalypt Forest along Blind Creek.

INDIRECT IMPACT

Potential impacts, and proposed avoidance and mitigation measures

Infection of native plants by Phytophthora cinnamomi

Introduction and Establishment of Exotic Rust Fungi of the order Pucciniales pathogenic on plants of the family Myrtaceae

Invasion of native plant communities by exotic perennial grasses

Invasion and establishment of exotic vines and scramblers

Invasion and establishment of Scotch broom (Cytisus scoparius)

At this point there is no evidence of pathogens in the study area. If there is potential for equipment and personnel to introduce pathogens to the area during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA 2011) would be implemented. These include:

The provision of vehicle and boot wash down facilities and ensure vehicles and footwear is free of soil before entering or exiting the site.

The risk of spreading pathogens and the mitigation measures required on site would be regularly communicated to staff and contractors during inductions and toolbox talks.

Construction works would be programmed to move from uninfected areas to any known infected areas.

Restriction of vehicles to designated tracks, trails and parking areas.

If required the above pathogen management measures would be implemented throughout the entire construction period.

Weed species are prevalent in disturbed habitats of the study area including roadside environments and cleared paddocks. A weed management plan would be developed as part of the CEMP. The details of the weed management plan would vary for each site but would include:

Taxa and potential sources of the weed species.

Weed management priorities and objectives.

Sensitive environmental areas within or adjacent to the site.

Location of weed infested areas.

Mechanical weed control methods such as slashing or mowing, as well as a r ange of herbicides to avoid the development of herbicide resistance.

Measures to prevent the spread of weeds.

A monitoring program to measure the success of weed management.

Strategic management with adjacent landowners.

Appropriate disposal of weed infested materials and soils to be identified in the CEMP.

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Threatening Process Potential impacts, and proposed avoidance and mitigation measures

Communication strategies to improve contractor awareness of weeds and weed management.

Predation by the feral cat (Felis The proposal may contribute to increased levels of predation on na tive catus) fauna from foxes, wild dogs, pigs and cats, through the impact of habitat

removal leading to displacement of resident fauna. Predation, habitat degradation,

There is some evidence of foxes preying on bandicoots at purpose built competition and disease transmission fauna underpasses that were placed in disturbed habitats (Harris et al. by feral pigs (Sus scrofa) 2010). However, these authors consider this is less likely where multiple

Predation and hy bridisation of feral structures are used, as is proposed, possibly minimising the potential for dogs (Canis lupus familiaris) predation. The proposed upgrade includes a c ombination of wildlife

crossing structures, which would include a bridge structure and four fauna Predation by the European red fox underpasses. (Vulpes vulpes) A flora and fauna management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation surrounding fauna crossing structures with the aim of minimising the potential for predation.

Woody debris and b ushrock would be r e-used on s ite for habitat improvement where applicable and would be detailed in CEMP. Suitable areas for re-use include the approaches to fauna underpasses, beneath the proposed bridge structure and would aim to minimise the potential for predation through providing cover for native fauna, and excluding potential feral predators.

Competition and grazing by the feral The clearing of vegetation may increase the value of the habitat for European rabbit (Oryctolagus rabbits (Oryctolagus cuniculus), feral deer (Family Cervidae) and feral cuniculus) goats (Capra hircus) in the study area over the long-term. Revegetation

of disturbed areas particularly formerly vegetated sites would assist in Competition and habitat degradation managing populations of these species. A flora and fauna management by feral goats (Capra hircus) plan would be developed as part of the CEMP which provides specific Herbivory and env ironmental details for the re-establishment of native vegetation on batters, cut faces, degradation caused by feral deer surrounding sediment basins and other areas disturbed during

construction.

Vegetation Clearing

The proposal would involve clearing of native vegetation and therefore involve the operation of a key threatening process.

Weed Invasion

The proposal could potentially involve the listed key threatening processes for the invasion of native vegetation by Lantana camara, exotic vines and s cramblers, and ex otic perennial grasses. Weed management would be implemented during the construction phase of the Proposal to limit the spread of exotic weed species, including appropriate disposal of exotic vegetative material and propagules.

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Altered Fire Regime It is unlikely that the natural fire regime would be altered from the Proposal.

Introduction of pests and diseases

There is potential for pests and diseases to be introduced from construction machinery such as Cinnamon Fungus (Phytophthora cinnamomi), and Myrtle Rust. Standard hygiene protocols would be implemented to avoid the introduction of pests and diseases to the study area.

Conclusion

As discussed this vegetation community along Dignams Creek is in moderate condition with some diversity of native flora and tree cover, shrub cover and threatened flora. However the vegetation community along the creek is also highly fragmented and h ighly disturbed from the past and adjacent land-use with a hi gh density of weeds and diminished structural and species diversity. Better quality examples of this community occur along Blind Creek where there will be some minor clearing (up to 0.1 hectares) on the edges of the riparian zone, however this area will be avoided where possible during construction and rehabilitation of any disturbed areas will be undertaken following construction. A number of mitigation measures have been recommended and would be implemented as part of an overall construction environmental management plan (CEMP). Avoidance and mitigation measures being implemented to reduce the impact to River-flat Eucalypt Forest comprise:

Appropriate road design to avoid this TEC where possible.

As part of the CEMP opportunities to avoid this TEC during construction will be investigated and the proposed clearing boundary adjacent to the TEC will be delineated on the ground to avoid accidental incursions into adjacent areas of this TEC.

Basic temporary fencing would be installed to indicate the limits of clearing and exclusion zones will be established in areas of this TEC outside these clearing limits.

A weed management plan would be developed as part of the CEMP to limit the spread of weeds to adjacent retained areas of this TEC.

Measures to prevent the introduction and/or spread of pests and disease causing agents such as bacteria and fungi into this TEC would be incorporated into the CEMP for the proposal.

A landscape management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction including areas of this TEC

The bridge structure over Dignams Creek will be designed and managed to minimise any potential impact to flow regimes which may indirectly impact this TEC.

This being considered the habitat to be removed is not considered important for the long-term survival of this TEC and the proposal is unlikely to have a s ignificant impact on t his ecological community. Therefore, an SIS is not required for this TEC.

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Square Raspwort (Haloragis exaltata subsp. exaltata)

Square Raspwort is a shrub that reaches 1.5 m tall with square, four-ribbed stems. The species is currently listed as vulnerable in NSW under the TSC Act; however there is a preliminary determination from 2008/2009 to delist this species from the TSC Act.

Square Raspwort occurs in four widely scattered localities in eastern NSW. It has a disjunct distribution in the Central Coast, South Coast and North Western Slopes botanical subdivisions of NSW (OEH 2013). Square Raspwort appears to require protected and shaded damp situations in riparian habitats with flowering specimens in NSW are recorded from November to January (OEH 2013).

(a) In the case of a threatened species, whether the action proposed is likely to have an adverse effect on the life cycle of the species such that a viable local population of the species is likely to be placed at risk of extinction.

The life-cycle and in particular the dispersal and germination of Square Raspwort appears associated with disturbance events including flooding, physical disturbance and fire (Miles and Cameron 2010). High levels of germination have been observed on areas of exposed bare earth with higher levels of light at ground level than would be present when the local vegetation community is intact (Miles and C ameron 2010). Considering this, it is unlikely that the proposal would adversely affect the life cycle of Square Raspwort, and r iparian areas disturbed during construction are likely to be recolonized by Square Raspwort.











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Square Raspwort (Haloragis exaltata subsp. exaltata) was frequently encountered along the edges of Dignams Creek within and surrounding the study area and is likely to be part of a l arge viable population. Square Raspwort has been found patchily along Dignams Creek from about 1.2 kilometres north-west of the bridge to where the creek enters Wallaga Lake, it is abundant on Snake Island in the Dignams Creek delta, and is scattered around the shoreline of Wallaga Lake, including the lower end of its other major tributary, Narira Creek (Miles and Cameron 2007).

Searches for Square Raspwort along Dignams Creek are summarized in Table F-1, comprising data collected during the current study as well as previous surveys. As can be seen from the results displayed the abundance of this species is very variable and h as increased since the original surveys. It is invariably found at sites where disturbance such as flooding, physical disturbance, or fire has exposed bare soil and created canopy gaps (Miles and Cameron 2007).

Table F-1: Results of surveys undertaken for Square Raspwort

Survey Results

Miles and Cameron (2007) Several hundred plants were identified scattered along 3 kilometre of creek undertook a survey of the frontage. An additional 3 kilometre searched immediately upstream had no plants. non-tidal areas of Dignams Creek during 2006.

NGH Environmental undertook targeted surveys during 2008

Found to fairly common along banks of Dignams Creek. Not identified along any tributaries of Dignams Creek. Approximately 75 plants were identified in the study area.

Targeted surveys undertaken by SKM during 2011.

Up to 900 plant clumps recorded along Dignams Creek approximately 150 metres to the north and 250 metres to the south of the Princes Highway. Dignams Creek was flooded prior to the surveys being undertaken with many plants partly buried beneath soil, fallen trees and other debris, and this disturbance event is likely to encourage further germination of the species. Of the approximate 900 plant clumps recorded in the wider area, approximately 40 would potentially impacted by the proposal. The distribution of Square Raspwort appeared to extend upstream and downstream of the area surveyed.

The proposal would result in the removal of approximately 50 individuals from the local population. The population would temporarily be fragmented from clearing impacts during construction, however vegetation clearing in riparian areas would be minimised where possible to avoid erosion of creek banks and therefore some areas of potential habitat would remain intact potentially including Square Raspwort individuals. Connectivity for the transfer of genetic material of this species would be maintained under the bridge structure and it is likely that Square Raspwort would colonise any disturbed areas following construction where sufficient light and moisture is available.

Prior to clearing the Square Raspwort from the construction footprint, individuals to be retained would be protected (i.e. flagged and identified to construction staff) where possible.

Only a small proportion of the local population of Square Raspwort would be permanently impacted from the proposal and it is highly likely that there would be regeneration of this species in areas disturbed during construction. The potential impacts would comprise removal of approximately 4.4 per cent of the population recorded along Dignams Creek 150 metres to the north and 250 metres to

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the south of the Princes Highway, and this proportion would be less when considering the broader population in the local area.

Considering the small proportion of plants removed relatively to the larger population in the local area and the high colonising and regenerative capacity of this species the proposal is considered unlikely to result in a long-term decrease to the population.




There is no r ecovery plan for Square Raspwort. Priority actions have been identified by OEH to assist the recovery of this species. The 15 identified priority actions comprise:

Validate old database records and amend those that are spatially incorrect.

Avoid frequent fire in known habitat; once fire ecology determined apply appropriate fire regime.

Develop Environmental Impact Assessment guidelines.

Prevent loss of known or potential habitat by adequate survey prior to any development.

Maintain populations ex situ at suitable botanic gardens, regional gardens or nurseries.

Consider known populations of Haloragis exaltata ssp exaltata on private land during environmental planning, as well as during biodiversity certification of environmental planning instruments for LGAs.

Consider location of known populations of Haloragis exaltata ssp exaltata during reserve planning.

Map extent of known populations.

Survey areas near known locations for additional populations of Haloragis exaltata ssp exaltata.

Determine and monitor current population size and demography and monitor, habitat condition and threats at known sites.

Determine fire ecology, juvenile period and seed longevity either by autecological study of Haloragis exaltata ssp exaltata or literature searches for information on similar species.

Consider VCA or similar agreement to manage populations on private land.

Control feral goats in known or potential habitat.

Conduct surveys before weed control at or near known localities of Haloragis exaltata ssp. exaltata.

Avoid using herbicides for weed control at known sites.

The proposal is consistent with these priority actions where relevant to the project such as avoidance of individuals and c onservation offsetting of populations. However priority actions associated with research and broader management obligations will not be implemented by the proposal.

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Threatening Process

DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 0.15 hectares of habitat for Square Raspwort. The proposed upgrade has been designed to minimise vegetation clearing where possible and di rect removal of Square Raspwort individuals and potential habitat would be minimized where possible during construction. Square Raspwort is known to colonise disturbed habitats and therefore it is likely that this species would regenerate in disturbed areas where there is sufficient light and moisture available.

INDIRECT IMPACT






At this point there is no evidence of pathogens in the study area. If there is potential for equipment and personnel to introduce pathogens to the area during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA 2011) would be implemented. These include:













A monitoring program to measure the success of weed

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management.





of disturbed areas particularly formerly vegetated sites would assist in Competition and habitat degradation managing populations of these species. A flora and fauna management by feral goats (Capra hircus) plan would be developed as part of the CEMP which provides specific Herbivory and env ironmental details for the re-establishment of native vegetation on batters, cut faces, degradation caused by feral deer surrounding sediment basins and other areas disturbed during

construction.

Vegetation Clearing - The proposal would involve clearing of native vegetation and therefore involve the operation of a key threatening process.

Weed Invasion - The proposal could potentially involve the listed key threatening processes for the invasion of native vegetation by Lantana camara, exotic vines and scramblers, and exotic perennial grasses. Weed management would be implemented during the construction phase of the Proposal to limit the spread of exotic weed species, including appropriate disposal of exotic vegetative material and propagules.

Altered Fire Regime -It is unlikely that the natural fire regime would be altered from the Proposal. Introduction of pests and diseases -There is potential for pests and diseases to be introduce from construction machinery such as Cinnamon Fungus (Phytophthora cinnamomi). Standard hygiene protocols would be implemented to avoid the introduction of pests and diseases to the study area.

Conclusion

A number of mitigation measures have been recommended and would be implemented as part of overall construction environmental management plan (CEMP). Avoidance and mitigation measures being implemented to reduce the impact to Square Raspwort comprise:

Appropriate road design to avoid this species where possible.

As part of the CEMP opportunities to avoid individuals of this species during construction will be investigated and individuals to be r etained would be protected (i.e. flagged and identified to construction staff) where possible.

Basic temporary fencing would be installed to indicate the limits of clearing and exclusion zones will be established in areas of habitat for Square Raspwort outside these clearing limits.

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A weed management plan would be developed as part of the CEMP to limit the spread of weeds to adjacent retained areas of habitat for Square Raspwort.

Measures to prevent the introduction and/or spread of pests and disease causing agents such as bacteria and fungi into habitat for Square Raspwort would be incorporated into the CEMP for the proposal.

A landscape management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction including areas of habitat for Square Raspwort.

The bridge structure over Dignams Creek will be designed and managed to minimise any potential impact to flow regimes which may indirectly impact habitat for Square Raspwort.

Considering the above proposed mitigation measures, the small proportion of plants removed relative to the larger population in the local area and the high colonising and regenerative capacity of this species the proposal is considered unlikely to result in a long-term decrease to the population and is therefore not considered to be a significant impact and an SIS is not required for this species.

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Threatened fauna

White-footed Dunnart

The White-footed Dunnart is listed as vulnerable in NSW under the TSC Act and occurs in Tasmania and along the Victorian and southern NSW coast. The Shoalhaven area is the species' northern-most limit. It has not been recorded west of the coastal escarpment with the western-most record being from Coolangubra State Forest, approximately 10 km south-east of Bombala.

The White-footed Dunnart is found in a range of different habitats across its distribution, including coastal dune vegetation, coastal forest, tussock grassland and sedgeland, heathland, woodland and forest. In NSW, the species seems to favour vegetation communities with an open und erstorey structure (contrasting with populations in Victoria which apparently prefer dense shrub and ground layers). It is patchily distributed across these habitats and, where present, typically occurs at low densities.

Breeding populations have been recorded in logged forest shortly after disturbance, but these usually do not persist as regeneration proceeds and a dense ground cover of vegetation establishes.

Home range and movement patterns of this species vary according to sex. Adult females usually have small, discrete home ranges, approximately 80 metres in length. Adult males have overlapping home ranges, approximately 100 metres in length, but are capable of making regular exploratory movements of up to 1 km.

White-footed Dunnarts appear to have only one short breeding season during their lifetime. In NSW and Victoria, mating occurs in late July and August. From August to September, up to ten young are born, each about 3 m m long. At two months, the young detach from the mothers’ teats and ar e suckled in the nest for about a month before dispersing.

The White-footed Dunnart is an o pportunistic carnivore that feeds on a variety of ground-dwelling invertebrates and, occasionally, small lizards.

They shelter in bark nests in hollows understanding or fallen timber, burrows in the ground, piles of logging debris, large grass clumps such as provided by Grass Trees Xanthorrhoea spp. and Cycads Macrozamia spp. and rock crevices.

Threats include loss and fragmentation of habitat resulting from land clearing for residential and agricultural developments. Modification and disturbance of habitat in coastal forest and foredune complex vegetation by camping and other recreational activities. Predation by foxes, cats and dogs. Collection of firewood from areas of habitat, including standing dead timber and logs on the ground. Fire regimes that result in continual absence of cover or thick regeneration may be deleterious. Studies conducted to date suggest that the species copes well in the short-term following events such as intensive logging, but populations may disappear within three years post-disturbance as the density of regrowth increases.

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Of the habitat within the proposal study area, the dry sclerophyll forest along the upper slopes and ridges of Gulaga and Kooraban National Park (Map Unit 1 Silvertop Ash open forest) would be considered suitable although marginal. The proposal would directly impact on around 4.6 hectares of this habitat types mainly in edge affected habitats along the existing highway. The remaining wet sclerophyll vegetation types and particularly gullies and slower slopes with dense understorey are not optimum habitat and their dominance in the study area may suggest that there are minimal opportunities for populations of the dunnart. There are very few records in the locality, with the majority occurring in more coastal areas dominated by dry forests and heath.

If present, a population is likely to occur at very low density and in restricted areas only. Clearing of habitat would remove sheltering and breeding habitat and if present may have a temporary impact on these life-cycle activities.

Larger areas of suitable habitat were noted further to the east and west of the proposal corridor in the ridges and low hills of Kooraban and Gulaga National Park and the area of habitat present in the study area is only relatively isolated and small in comparison to these. There is greater potential for larger viable populations to occur outside of the proposal area.


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Of the habitat within the proposal study area, the dry sclerophyll forest along the upper slopes and ridges of Gulaga and Kooraban National Park (Map Unit 1 Silvertop Ash open forest) would be considered suitable although marginal. The proposal would directly impact on around 4.6 hectares of this habitat type mainly in edge affected habitats along the existing highway. The remaining wet sclerophyll vegetation types and particularly gullies and slower slopes with dense understorey are not optimum habitat and their dominance in the study area may suggest that there are minimal opportunities for populations of the dunnart. There are very few records in the locality, with the majority occurring in more coastal areas dominated by dry forests and heath.

The proposal involves some widening of the existing road but mostly a new clearing to accommodate the upgrade. There is currently very limited connectivity under the existing highway and no fauna underpasses and c onnectivity is therefore likely to be improved from this current situation with the construction of purpose built large underpasses including a bridge at Dignams Creek.

If present, a popu lation is likely to occur at very low density and in restricted areas only. Lar ger areas of suitable habitat were noted further to the east and west of the proposal corridor in the ridges and low hills of Kooraban and Gulaga National Park and the area of habitat present in the study area is only relatively isolated and small in comparison to these and not considered an important area of habitat.


Critical habitat has not been declared for this species.


The Office of Environment and Heritage has identified 10 priority actions to help recover the White-footed Dunnart in New South Wales.

Conduct population surveys and identify key habitats and populations.

Promote community awareness to prevent collection of firewood (standing dead timber and logs on the ground) from areas of habitat and to prevent domestic dogs and cats roaming in habitats near urban areas.

Develop and distribute EIA guidelines for decision makers.

Protect key habitat and populations on private and public land.

Assess fire and logging impacts on populations and habitat.

Monitor known populations at selected sites.

Control and monitor abundance of feral predators (cats, foxes and dogs) and rabbits around key populations.

Control weeds (e.g., Bitou Bush) where they are present near key habitats.

Collect hair samples to enable identification of genetic structure of populations across the species range.

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Conduct ecological research on p opulation ecology, habitat use and relationships with seral stages of vegetation communities.

The study area is not identified as a key population or key habitat for this species and therefore none of these actions are relevant to the proposal.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of foraging habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat resilience, habitat degradation from feral herbivores and increased predation from feral predators.

Threatening Process

DIRECT IMPACT


Clearing of native vegetation The proposal would result in the removal of approximately 20 hectares of native vegetation considered potential habitat for the species. Proposed avoidance and mitigation measures include:

The proposed upgrade has been designed to minimise vegetation clearing where possible and minimise potential impacts to Dunnart.

Revegetation of obsolete sections of the existing highway would occur.

INDIRECT IMPACT

Infection of native plants by At this point there is no evidence of pathogens in the study area. If there Phytophthora cinnamomi is potential for equipment and personnel to introduce pathogens to the

area during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA 2011) would be implemented. These include:

The provision of vehicle and boot wash down facilities and Introduction and Establishment of ensure vehicles and footwear is free of soil before entering or Exotic Rust Fungi of the order exiting the site. Pucciniales pathogenic on plants of The risk of spreading pathogens and the mitigation measures the family Myrtaceae required on site would be regularly communicated to staff and

contractors during inductions and toolbox talks.




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Invasion of native plant communities Weed species are prevalent in disturbed habitats of the study area by exotic perennial grasses including roadside environments and cleared paddocks. A weed

management plan would be developed as part of the CEMP. The details of the weed management plan would vary for each site but would include:

Invasion and establishment of exotic Taxa and potential sources of the weed species. vines and scramblers Weed management priorities and objectives. Invasion and establishment of Scotch Sensitive environmental areas within or adjacent to the site. broom (Cytisus scoparius)















of disturbed areas particularly formerly vegetated sites would assist in Competition and habitat degradation

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by feral goats (Capra hircus) managing populations of these species. A flora and fauna management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction.

Herbivory and env ironmental degradation caused by feral deer

Conclusion

If the species is present, populations are likely to occur at very low density and in restricted areas only. L arger areas of suitable habitat were noted further to the east and west of the proposal corridor in the ridges and low hills of Kooraban and Gulaga National Park and the area of habitat present in the study area is only relatively isolated and s mall in comparison to these and n ot considered an important area of habitat. The proposal is unlikely to significantly impact on the White-footed Dunnart and therefore an SIS is not required.

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Spotted-tailed Quoll

The Spotted-tailed Quoll is listed as vulnerable in NSW under the TSC Act. The current distribution of this species is the coast and r anges of eastern Australia from southern Queensland to the Victorian/ South Australian border and Tasmania. T he mainland range of this species has been fragmented and s ignificantly reduced and is now disjunct over much of its former distribution. Spotted-tailed Quolls have been reported inhabiting a wide range of habitats including rainforest, wet and dry sclerophyll forest, woodland, coastal heathland and inland riparian forest. Occasionally, the species has been recorded in rock outcrops or other treeless areas (Edgar & Belcher 1995). The species requires extensive home ranges, and i s generally so confined to localities which contain extensive and continuous tree cover.

Populations of the Spotted-tailed Quoll have been much reduced through habitat loss, and the species is currently sparsely distributed and rare. Land clearance for agricultural and urban development, as well as disease (possibly a form of toxoplasmosis - which is caused by a protozoan parasite prevalent in feral cats) and persecution have significantly reduced populations of this species, and the distribution of the Spotted-tailed Quoll is heavily fragmented as a result. Spotted-tailed Quolls compete for resources and s helter with Foxes, Feral Dogs and Feral Cats, and competition with these species may have an adverse impact on populations (Edgar & Belcher 1995). Spotted-tailed Quolls are also susceptible to baits laid for wild dogs.

A solitary, generally nocturnal (although some foraging, and sun-basking takes place during the day) and semi-arboreal species, the Spotted-tailed Quoll preys on a variety of species, ranging in size from small wallabies to reptiles and insects, as well as plants. Medium-sized terrestrial and arboreal mammals, such as Brushtail Possums, Rats, small macropods and Rabbits, comprise about two-thirds of the diet in south-east Australia, with birds (and their young) and carrion also being important dietary components. The species has been persecuted as a result of attacks on domestic poultry. Much of the foraging of this species is undertaken on the ground, but some foraging in trees is undertaken, and trees are also used as vantage points to detect prey and pounce on prey. Spotted-tailed Quolls, as opportunistic predators, utilise extensive home ranges which are estimated to be between 500 - 1 000 hectares (Australian Museum Business Services 1995). Movements of up to several kilometres in a single night have been recorded.

Both males and females mature when about one year old and mating occurs between April and July. The average litter size is five and young are fully independent at 18 weeks. Den and nest sites have been recorded in caves, rock crevices, tree hollows and hollow logs (Edgar & Belcher 1995).

Spotted-tailed Quolls are known and predicted to occur in the locality and the range of habitats including large patches of native vegetation as well as farmland render the area suitable for this species. Potential impacts for the species are associated with the loss of habitat including potential den sites, habitat for prey species, fragmentation and the barrier effect of the highway potentially leading to increased genetic isolation and d ecreased dispersal ability. The species is known to frequent roadsides feeding on roadkill, thereby placing them at risk of vehicle strike.

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Life-cycle attribute include hunting and suitable habitat for prey species, shelter and breeding microhabitats and dispersal of juveniles and movements of adults to account for home range areas. The severity of the impact in the locality is likely to be minor considering the large home-range of the species occurring at low densities and wide ranging dispersal abilities. Suitable habitat for the species is very widespread in the locality within conservation reserves and pr ivate lands and t he proposal would remove approximately 20 hectares of habitat that could potentially be used or form part of the home range of a small number of individuals.

The potential barrier effect and f ragmentation impacts would be adequately mitigated with the installation of the targeted fauna connectivity measures for this species (e.g. underpasses and bridge).The existing highway presents barriers to east-west movement that would be improved by the addition of combined and dedicated fauna underpasses.

The species typically has a large home range and occupies a diversity of habitat types. It is therefore difficult to identify the area of occupancy and home range. Theoretically, quolls could occur in any of the larger forest fragments of the study area. Preferred habitat includes dry and moist sclerophyll forests and may include adjacent modified patches of forest on farmland. Suitable habitat is well represented in the larger fragments of forest in the region associated with several state forests and conservation reserves. The potential impact to habitat for prey species and life-cycle activities associated with the proposal represents a very small proportion of available habitat approximately in this locality.

Viable local populations could be expected to occur in this region and the impacts to life-cycle activities would be temporary and only likely to affect a small number of individuals if present, give the scale of the proposal in relation to habitat availability in the region. The proposal is considered unlikely to lead to risk of extinction for local populations of Spotted-tailed Quoll.


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The proposal would involve the removal of approximately 20 hectares of potential habitat for prey species of the quoll. The habitat to be cleared along the roadside is considered only marginal as denning or sheltering habitat for this species due to an absence of caves and low abundance of large hollow logs. Larger logs are present throughout both national parks and w ere noted in the surrounding landscape.

There are large areas of potential habitat for this species associated with Kooraban and G ulaga National Park and also several other reserves and state forests in the region. There are multiple records for this species in the region extending to the south to Bega and to the north and west with very large forested areas on the eastern slopes of the Great Dividing Range. The study area may be important habitat for local population and would represent an important link in the landscape. The potential impact to habitat represents a very small proportion of the available habitat within 15 kilometre radius of the proposal footprint.

Vegetation clearing for the proposal would result in greater distance between habitats on either side of the highway no new-edges would be created and no areas of habitat would become isolated. The proposal involves some widening of the existing road but mostly a new clearing to accommodate the upgrade. There is currently very limited connectivity under the existing highway and no fauna underpasses. Connectivity for Spotted-tailed Quoll is likely to be improved from this current situation with the construction of purpose built large underpasses including a bridge at Dignams Creek.

Habitats adjacent to the road and within the proposal footprint provide potential resources for this species in terms of an area of habitat for likely prey species and an area of potential shelter in the form of habitat hollows (logs, trees or stags), however this area of habitat is currently positioned adjacent an existing highway which may reduce its suitability particularly when considering it is part of a large expanse of remnant habitat continuing to the west, north and south.




A draft national recovery plan for the Spotted-tailed Quoll is currently being prepared. In NSW, the Threatened Species Priorities Action Statement lists recovery actions for all threatened species. A total of 33 recovery actions are listed for the Spotted-tailed Quoll. These actions focus on addressing current knowledge gaps and managing the threats to quoll populations as identified through

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scientific research. Mortality from collisions with vehicles is a known threat to this species and has been considered in this proposal through the provision of dedicated underpass structures targeting this species.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of foraging and sheltering habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality, habitat degradation from feral herbivores and increased predation from and competition with feral predators.


DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 20 hectares of native vegetation supporting hollow-bearing trees, dead wood and dead

Loss of hollow-bearing trees trees, and bushrock. Proposed avoidance and mitigation measures include: Removal of dead wood and dead

trees The proposed upgrade has been designed to minimise vegetation clearing where possible and minimise potential impacts to threatened species habitat.

Targeted mitigation measures would be developed as part of the Construction Environment Management Plan (CEMP) which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction.

Woody debris and bushrock would be re-used on site for habitat improvement where applicable and would be detailed in the landscape management plan/CEMP. Suitable areas for re-use may include the approaches to fauna underpasses, beneath the proposed bridge structure at Dignams Creek and r ehabilitation areas as part of the offset strategy.

INDIRECT IMPACT



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Predation by the feral cat (Felis catus)

Predation, habitat degradation, competition and disease transmission by feral pigs (Sus scrofa)

Predation and hy bridisation of feral dogs (Canis lupus familiaris)

Predation by the European red fox (Vulpes vulpes)

















The proposal may contribute to increased levels of predation on na tive fauna from foxes, wild dogs, pigs and cats, through the impact of habitat removal leading to displacement of resident fauna.

An offset plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation surrounding fauna crossing structures and in cleared lands with the aim of minimising the potential for predation.

Woody debris and b ushrock would be r e-used on site for habitat improvement where applicable and would be d etailed in the offset plan/CEMP. Suitable areas for re-use include the approaches to fauna underpasses, beneath the proposed bridge structure a Dignams Creek and would aim to minimise the potential for predation through providing

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cover for native fauna, and excluding potential feral predators.

Competition and grazing by the feral European rabbit (Oryctolagus cuniculus)

The clearing of vegetation may increase the value of the habitat for rabbits (Oryctolagus cuniculus), feral deer (Family Cervidae) and feral goats (Capra hircus) in the study area over the long-term. Revegetation of disturbed areas particularly formerly vegetated sites would assist in managing populations of these species. An offset plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction.

Competition and habitat degradation by feral goats (Capra hircus)


Conclusion

Potential habitat for the Spotted-tailed Quoll and prey species is well represented across the landscape and region from a variety of eucalypt forest types including natural and disturbed habitats. This includes potential habitats for life-cycle activities of breeding, hunting shelter and movements. Considering the relatively small area of potential habitat for prey species and shelter or denning habitat that would be removed relative to the extent of similar habitats in the locality the proposal is considered unlikely to constitute a significant impact to this species and an SIS is not required.

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Yellow-bellied Glider

The Yellow-bellied Glider is listed as a vulnerable species in NSW under the TSC Act. Yellow-bellied Gliders are distributed along the coast and montane ranges of eastern Australia from central Queensland to south-east Victorian, with isolated populations also occurring in the Atherton Tablelands, Queensland and south-west Victoria. This species has a patchy distribution. Known to occur in a v ariety of habitats, Yellow-bellied Gliders are usually associated with tall, mature wet eucalypt forest in high rainfall areas. They are present at low densities, even in areas of preferred habitat, probably as a result of the low food availability and their territorial nature.

The low nutritional value of the major food of this species (sap) requires individuals to spend large amounts of time foraging within extensive home ranges. As a result, this species is apparently declining mainly through the loss and fragmentation of habitat (Russell 1995). C learance for agricultural and urban development and intensive forestry practices has probably had a significant effect on Y ellow-bellied Glider populations. L oss of tree hollows and foraging areas poses the greatest threats to remnant populations. Fire may adversely affect some populations of this species.

The diet of this species includes plant exudates (sap, nectar, honeydew and manna) as well as insects. Sap is tapped from the trunks of trees via chewed "V" shaped incisions or in some cases extended vertical incisions (Goldingay & Kavanagh 1991). T ree species used varies according to locations and habitats, and although none of the species in the study area have been identified as food trees, some of these species may potentially be utilised by the species. The shedding of bark by tree species is considered important for the gathering of invertebrates and honeydew. Hollows for nest sites are essential, as are suitable food trees. Den sites are often, but not always, located in mature, living smooth-barked eucalypts.

This species is known to have a large home range of more than 35 h ectares and may travel in excess of 2 kilometres from the den to forage in a single night. The resident pair and their offspring are territorial and home ranges do not overlap. Population density is low (0.05 - 0.14 individuals per hectare), with family groups of 3 - 4, and sometimes 6, animals usual for New South Wales. The largest trees within the home range are used for both roosting and feeding, and certain tree species are selected for these purposes (Goldingay & Kavanagh 1993). In south-eastern New South Wales young are born between June and December and this may be tied to the availability of exudates for food. Weaning may coincide with the availability of arthropods (Goldingay & Kavanagh 1991). The litter size is one, pouch life is about 100 days and young are left in the nest for a further 2 months. Dispersal from the family group occurs at 18 - 24 months when full body size is reached (Craig 1985).


Yellow-bellied Gliders were recorded at two locations, firstly to the south of Dignams Creek Road approximately 200 m within riparian habitat near Blinds Creek on pr ivate land and secondly within Kooraban National Park at the furthest southern end of the proposal also within riparian forest.

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The hollow tree survey identified a higher density of hollow-trees on the western side of the highway than the eastern side and a higher density within Kooraban National Park than other parts of the study corridor. This included observation of an important Yellow-bellied Glider sap feeding tree and a number of possible den trees in Kooraban National Park. Two yellow-bellied gliders were observed on the sap tree and this tree is expected to be an important feature in the home range of at least one family group of gliders. The habitat to the west of the highway in Kooraban NP is of better quality than on the ridge to the east of the highway in Gulaga NP which is considered marginal.

The location of the sap feeding tree was considered in the final design of the upgrade such that it would be avoided from direct impact. There may be indirect impacts from traffic noise and lights. The location of actual den sites was not determined, and based on the habitat tree survey several habitat trees identified as potential den s ites would be r emoved. The proposal is likely to impact on t he extent of food and shelter resources from the territory of one family group of gliders in this location and potentially movements for dispersal to the east across the highway. Yellow-bellied gliders are expected to occur in low density in the study area and considerable areas of potential habitat remain outside of the proposal corridor within the national park and c ontinuing the west and north of the proposal. This suggests that opportunities for future dispersal of young and expansion of the home range for this family group exist. This also suggests that local populations of gliders extend to the west and north of the proposal as was identified at Blinds Creek and that the habitat removal for the southern end of the proposal is unlikely to lead to the local extinction of the population.


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Yellow-bellied Gliders were recorded at two locations, firstly to the south of Dignams Creek Road approximately 200 m within riparian habitat near Blinds Creek on private land and secondly within Kooraban National Park at the furthest southern end of the proposal also within riparian forest. The habitat in the Blinds Creek area would not be directly impacted by the proposal. At the southern end of the proposal around 5-6 hectares of foraging and denning habitat could be removed from the home range territory of a family group which may include the loss of multiple den sites and possible sap feeding trees. However an important sap feeding tree and several other potential den trees were recorded outside of the proposal corridor.

Considerable areas of potential habitat remain outside of the proposal corridor within the national park and c ontinuing to the west and north of the proposal suggesting that opportunities for future dispersal of young and expansion of the home range for this family group exist. This also suggests that local populations of gliders extend to the west and north of the proposal as was identified at Blinds Creek and that the habitat removal for the southern end of the proposal during stage 2, may impact on a family group of gliders but is unlikely to negatively affect the long-term survival of the species in this locality.




There is a r ecovery plan for the Yellow-bellied Glider. Considering the high proportion of habitat outside the proposal area for this species and the proposed mitigation measures to minimise habitat removal and facilitate natural movements of fauna across the proposal corridor, the proposal is consistent with the objectives of the recovery plan.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of foraging and sheltering habitat and t he removal of hollow-bearing trees. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality, increased competition with feral honey bees for hollow resources, habitat degradation from feral herbivores and increased predation from feral predators.

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DIRECT IMPACT


Clearing of native vegetation The proposal would result in the removal of approximately 20 hectares of native vegetation much of which would be considered to support hollow-

Loss of hollow-bearing trees bearing trees, dead wood and dead trees suitable to the Yellow-bellied Glider. Proposed avoidance and mitigation measures include: Removal of dead wood and dead

trees The proposed upgrade has been designed to minimise vegetation clearing where possible and minimise potential impacts to threatened species habitat.

Revegetation of obsolete sections of the existing highway.

INDIRECT IMPACT


area during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA

Introduction and Establishment of 2011) would be implemented. These include: Exotic Rust Fungi of the order The provision of vehicle and boot wash down facilities and Pucciniales pathogenic on plants of ensure vehicles and footwear is free of soil before entering or the family Myrtaceae exiting the site.





Invasion of native plant communities Weed species are prevalent in disturbed habitats of the study area by exotic perennial grasses including roadside environments and cleared paddocks. A weed

management plan would be developed as part of the CEMP. The details of the weed management plan would vary for each site but would include:

Invasion and establishment of exotic Taxa and potential sources of the weed species. vines and scramblers

Weed management priorities and objectives. Invasion and establishment of Scotch Sensitive environmental areas within or adjacent to the site. broom (Cytisus scoparius)






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Conclusion

Avoidance and mitigation measures specific to Yellow-bellied Glider implemented by the proposal include:

A rope canopy bridge that is designed for glider use to be l ocated within the National Parks adjacent to the Yellow bellied Glider habitat (Stage 2 only).

Avoidance of identified areas of habitat currently occupied by the Yellow-bellied Glider, including an important sap feeding tree and several hollow-bearing habitat trees.

Considering the above avoidance and mitigation measures and the small area of optimal habitat that would be removed relative to the extent of similar habitats in the locality the proposal is unlikely to constitute a significant impact to local populations of Yellow-bellied Glider. Habitat removal for the southern end of the proposal may have an impact on a family group of gliders but is unlikely to negatively affect the long-term survival of the species in this locality.

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Brush-tailed Phascogale

The Brush-tailed Phascogale is listed as vulnerable in NSW under the TSC Act. The Brush-tailed Phascogale typically prefers dry sclerophyll open forest with sparse groundcover of herbs, grasses, shrubs or leaf litter. An agile climber foraging preferentially in rough barked trees of 25 cm DBH or greater where it feeds mostly on arthropods but would also eat other invertebrates, nectar and sometimes small vertebrates.

Females have exclusive territories of approximately 20 - 40 ha, while males have overlapping territories often greater than 100 ha. Phascogales den and shelter in tree hollows with entrances 2.5 - 4 cm wide and use many different hollows over a short time span.


The optimum habitat in the study area would include the Silvertop Ash Open Forest (map unit 1). They may also inhabit wet sclerophyll forest which includes map units 2 and 3. The habitats present occur in varying condition according to the land-use activates which have included logging and selective clearing.

The proposal would result in the clearing of about 25.4 hectares of native vegetation, thereby removing areas of habitat for this species. This loss of habitat comprises around 4.6 hectares of dry open forest mainly along ridge and upper slope areas which is optimum for phascogale and 16.4 hectares of wet sclerophyll forest mainly in lower slopes and sheltered slopes and g ullies which would be considered more marginal.

The habitat tree survey was conducted along the length of the proposal centred on t he proposal footprint. A total of 51 habitat trees were recorded from the current survey and t he previous investigation (NGH 2010). Tree hollows were found to be more common in gullies and riparian areas than ridge top habitats preferred by the species and more common at the southern end of the proposal in Kooraban National Park. Large areas of optimum habitat were also noted in ridges and low hills beyond the corridor in reserved lands and private lands at a gr eater distance from the highway.

The area of this habitat to be disturbed relative to the extent of suitable habitats suggests that viable local populations would extent at through multiple areas of the locality both east and west of the highway. The clearing involved with this proposal would have impacts on the life-cycle of a relatively small proportion of the local population if present and unlikely to lead to extinction in this locality.


n/a

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n/a





The proposal would result in the clearing of about 25.4 hectares of native vegetation, thereby removing areas of habitat for this species. This loss of habitat comprises around 4.6 hectares of dry open forest mainly along ridge and upper slope areas which is optimum for phascogale and 16.4 hectares of wet sclerophyll forest mainly in lower slopes and sheltered slopes and g ullies which would be considered more marginal.

The proposal involves some widening of the existing road but mostly a new clearing to accommodate the upgrade. There is currently very limited connectivity under the existing highway and no fauna underpasses and c onnectivity is therefore likely to be improved from this current situation with the construction of purpose built large underpasses including a bridge at Dignams Creek and a canopy rope crossing between the two National Parks.

If present, a popu lation is likely to occur at very low density and in restricted areas only. Lar ger areas of suitable habitat were noted further to the east and west of the proposal corridor in the ridges and low hills of Kooraban and Gulaga National Park and the area of habitat present in the study area is only relatively isolated and small in comparison to these and not considered an important area of habitat.




The Office of Environment and Heritage has identified 7 priority actions to help recover the Brush-tailed Phascogale in New South Wales.

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Establish a long term monitoring program targeting at least 30 populations across the known range of Brush-tailed Phascogales. The program would incorporate sites used for experimental fox control (as per Fox TAP).

Undertake a targeted community education program that raises awareness about threats such as predation from cats.

Develop and provide environmental assessment guidelines for Local Councils and ot her consent or determining authorities to enable adequate consideration of the potential impacts of activities or actions on phascogales.

Monitor the effectiveness of forestry threatened species licence conditions and refine and negotiate changes if required.

Undertake research into the impact of hazard reduction burn practices.

Undertake fox and wild dog control at priority sites.

Design and implement an ecological burn (Dinner Creek) including habitat requirements of the species in Demon Nature Reserve.

There are no recognized key habitats or populations for this species in the study area and none of these actions are relevant to the proposal or study area.




DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 16.4 hectares of native vegetation supporting secondary feed tree species. Proposed avoidance and mitigation measures include: The proposed upgrade has been de signed to minimise vegetation

clearing where possible and minimise potential impacts to Brush-tailed Phascogale habitat.


INDIRECT IMPACT

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Predation and hy bridisation of feral dogs (Canis lupus familiaris)


At this point there is no evidence of pathogens in the study area. If there is potential for equipment and personnel to introduce pathogens to the area during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA 2011) would be implemented. These include: The provision of vehicle and boot wash down facilities and ensure

vehicles and footwear is free of soil before entering or exiting the site.





Weed species are prevalent in disturbed habitats of the study area including roadside environments and cleared paddocks. A weed management plan would be developed as part of the CEMP. The details of the weed management plan would vary for each site but would include: Taxa and potential sources of the weed species.




Mechanical weed control methods such as slashing or mowing, as well as a range of herbicides to avoid the development of herbicide resistance.







There is some evidence of foxes preying on bandicoots at purpose built fauna underpasses that were placed in disturbed habitats (Harris et al. 2010). However, these authors consider this is less likely where multiple structures are used, as is proposed, possibly minimising the potential for predation. The proposed upgrade includes a c ombination of wildlife crossing structures, which would include a bridge structure and four fauna underpasses.

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A flora and fauna management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation surrounding fauna crossing structures with the aim of minimising the potential for predation.




of disturbed areas particularly formerly vegetated sites would assist in managing populations of these species. A flora and fauna management plan would be developed as part of the CEMP which provides specific

Herbivory and environmental details for the re-establishment of native vegetation on batters, cut faces, degradation caused by feral deer surrounding sediment basins and other areas disturbed during

construction.

Conclusion

If this species is present, a population of the Brush-tailed Phascogale is likely to occur at a very low density and in restricted areas only. Larger areas of suitable habitat were noted further to the east and west of the proposal corridor in the ridges and low hills of Kooraban and Gulaga National Park and the area of habitat present in the study area is only relatively isolated and small in comparison to these and not considered an i mportant area of habitat. The proposal is unlikely to significantly impact upon the Brush-tailed Phascogale.

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Koala

The Koala is listed as vulnerable in NSW under the TSC Act. The Koala is a folivore, feeding on some Eucalypt species. The Koala is found in a variety of habitats where suitable food trees occur. The Koala is adversely affected by habitat loss and fragmentation, wild fire, predation and disease. In fragmented habitats, roadkills and dog attacks are significant problems. G enetic introgression can be a s erious threat to high density populations in isolated habitats. H abitat preservation and linking of isolates with habitat corridors is essential for the long term survival of Koala populations (Martin & Handasyde 1995).

Koalas are generally solitary except during the mating season and have a home range of about 3 hectares (although the size of this area is influenced by the distribution, abundance and quality of feeding resources). In dense populations, home ranges may overlap but appear to be discrete at lower densities (Martin & Handasyde 1995). Long movements in search of a mate or new food source are sometimes undertaken, signifying the importance of dispersal corridors in secure Koala habitat (Phillips 1990).


No Koala scats were recorded from the survey of 600 t rees on both sides of the highway (500 m wide) within the length of the study area (refer Appendix H). Any Koala activity in the study area is considered to be v ery low and the survey results suggest that the habitats adjoining the proposal corridor may only be used occasionally by dispersing individuals rather than supporting a portion of the local population or the home range of an individual.

In recent Koala surveys conducted by Allen (2011) in Kooraban and Gulaga National Park only 8% of the grid-sites assessed had evidence of Koalas in the Kooraban/Gulaga area, and none of these were in proximity to the road corridor. Compared with most areas where this kind of survey is undertaken in the southern forests (e.g. Allen et al 2010), this success rate is very low. These results suggest probably only 5-15 Koalas are surviving in the approximately 6,000 hectares of forests assessed by Allen (2011). No Koala activity was reported close the current study area.

The two areas in the Kooraban National Park reported by Allen (2011) where Koalas (the Sam’s Ridge and Jimmy’s Creek areas) are persisting are those where Koalas had been identified previously both in anecdotal reports and in previous surveys. Sam’s Ridge area is several kilometres to the west of the study area and Jimmy’s Creek further north-west. The continued persistence in these areas over at least several decades indicates some stability with these two breeding associations (Allen 2011).

By the 1960’s Koalas were known to be persisting to the east of the Princes Highway and south of Dignams Creek in what was to become the Wallaga Lake, and then in 2000, was incorporated in the Gulaga National Park. The species was also known from Dignams Hill, immediately to the west of this area which is incised by the Princes Highway. The evidence reported by Allen (2011) and in recent surveys of the regional area indicates that these eastern populations may be extinct, however

215


considerable areas of habitat with Koala feed tree species remain to the east of the highway in Gulaga National Park to Wallaga Lake area.

Recent research in the south coast region (DECCW 2010c) has established that eucalypt communities in which Eucalyptus longifolia (woollybutt), E. globoidea (white stringybark), and E. muelleriana (yellow stringybark), E. cypellocarpa (monkey gum), E. bosistoana (coastal grey box), E. tricarpa (red ironbark) and E. sieberi (silvertop ash) occur sustains the known Koala populations in this part of the region.

These feed trees are locally important and associated with frequent Koala activity (DECCW, 2010c), and are also recognised in the south coast area as secondary and supplementary Koala food trees (with the exception of E. tricarpa and E. sieberi) (DECC, 2008). The feed tree species are identified in this biodiversity assessment within Map Units 1, 2, 3 identified in the study area. The presence of these habitats containing known feed tree species would be considered potential habitat that is important for the survival of Koalas. This is reinforced by the presence of a regional corridor linking Kooraban and Gulaga National Park.

White stringybark, yellow stringybark, monkey gum and silvertop ash are all components of the vegetation map units 1 a nd 2 a nd 3 identified in the study area and the vegetation types are considered important for Koala in the region. The proposal would remove up to 19.9 hectares of this Koala habitat, although Koala activity was not reported from the targeted survey and there is no indication that the study area is within the home range area of a Koala. The habitats to be removed are expected to be within a corridor for potential dispersal of Koalas to suitable habitats to the east.

Apart from the loss of habitat, Koalas may be impacted by vehicle strike and a reduced ability to disperse and colonise other suitable habitats to the east of the highway. Currently connectivity for the Koala is restricted by the existing highway and there are no suitable underpasses. The final stage of the proposed upgrade would aim to facilitate the natural movements of Koala across the proposal corridor with suitable underpasses including two dedicated and two combined underpasses (two 3 m etre and two 2.4 metre square culverts) and a br idge structure over Dignams Creek and fauna fencing.

The proposal would remove a relatively small area of habitat containing known Koala feed tress but not known to be currently occupied by local populations or forming the home range of an individual. This clearing of habitat is considered minimal in relation to the extent of similar habitats containing feed tree species known to be present throughout Kooraban and Gulaga National Park and surrounds (c. 6000 ha) (Allen 2011). The work by Allen (2011) suggests that the study area may constitute a potential east-west dispersal corridor for Koalas to access and colonise potential habitats in these reserves. These factors in addition to the proposed inclusion of targeted underpass structures aimed to facilitate the natural movements of Koala across the proposal corridor between these two reserves suggest that the proposal is unlikely to lead to an increased risk of extinction for the known populations noted from the locality.

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n/a




n/a





The data used in this assessment includes detailed descriptions gathered for the vegetation community types and floristic composition and the proposal vegetation community mapping and other broad-scale mapping of the region as reported in Tozer et al (2010).

In addition to this recent research in the south coast region (DECCW 2010c) has established that eucalypt communities in which Eucalyptus longifolia (woollybutt), E. globoidea (white stringybark), and E. muelleriana (yellow stringybark), E. cypellocarpa (monkey gum), E. bosistoana (coastal grey box), E. tricarpa (red ironbark) and E. sieberi (silvertop ash) occur sustains the known Koala populations in this part of the region.

These feed trees are locally important and associated with frequent Koala activity (DECCW, 2010c), and are also recognised in the south coast area as secondary and supplementary Koala food trees (with the exception of E. tricarpa and E. sieberi) (DECC, 2008). There are no r ecognised primary feed tree species from the south coast region (DECC, 20080 recorded in the study area and only one secondary feed tree species, Monkey Gum (Eucalyptus cypellocarpa). The feed tree species identified in this biodiversity assessment occur within Map Units 1, 2, 3 identified in the study area (refer Table below).

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M U

Vegetation types identified in the study area

Food tree species south coast region (DECC 2008) (% cover)

Important food trees south coast region (DECCW 2010c) additional to DECC (2008)

Primary food trees Bega Valley and Eurobodalla LGA (AKF 2012) additional to DECC (2008) and DECCW (2010c)

Habitat critical to Koala survival based on DSEWPaC (2012)

Habitat category, Callaghan unpublished in DECC (2008)

Primary Secondary Supplementary Primary Other

1 Silvertop Ash – Stringybark dry open forest

None Monkey Gum (E. cypellocarpa) (<5%), Yertchuk (E. consideniana) (<5%),

Coast Grey Box (E. bosistoana) (<5%)

Blue-leaved Stringybark (E. agglomerata) (>30%),

White Stringybark (E. globoidea) (10%),

Yellow Stringybark (E. muelleriana) (5%),

Silvertop Ash (E. sieberi) (>30%),

Red Ironbark (E. tricarpa) (<5%),

Rough-barked Apple (Angophora floribunda) (20%)

Black She-oak (Allocasuarina littoralis) (mid-storey 5-20%)

Monkey Gum (E. cypellocarpa) (<5%)

No Secondary habitat (class B)

2 White Stringybark dry open forest

None Monkey Gum (E. cypellocarpa) (10%),

Coast Grey Box (E. bosistoana) (<5%), Woollybutt (E. longifolia) (<5%), Blue Box (E.

Yellow Stringybark (E. muelleriana) (>30%),

White Stringybark (E. globoidea) (>30%),

Blue-leaved Stringybark (E. agglomerata) (5%)

Silvertop Ash (E. sieberi), (5%),

Rough-barked Apple (Angophora floribunda) (20%),



No Secondary habitat (class C)

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baueriana) (<5%)

3 Bangalay/ Blue Gum sheltered

None Monkey Gum (E. cypellocarpa)

Yellow Stringybark (E. muelleriana)



Bangalay (E. botryoides) (>30%) occurs


forest (<5%) (>30%), as a hybrid with

White Stringybark (E. globoidea) (10%)

Sydney Blue Gum (Eucalyptus saligna)

4 River Peppermint

None None None Rough-barked Apple (Angophora floribunda)

Bangalay (E. botryoides)

No Tertiary habitat

– Rough- (5%) (10%) occurs as barked a hybrid with Apple moist Sydney Blue shrubby forest

Gum (Eucalyptus saligna)

5 Riparian forest

None None None Rough-barked Apple (Angophora floribunda) (5%)

Bangalay (E. botryoides) (5%) occurs as a hybrid with Sydney Blue Gum

No Tertiary habitat

(Eucalyptus saligna)

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According to DECC (2008) Map uni t 1 i s secondary habitat (class B), map units 2 and 3 ar e secondary habitat (class C) and the riparian habitat is classed as tertiary habitat. The proposal would remove a total of 19.9 hectares of secondary habitat for Koalas and 0.7 hectares of tertiary habitat (potential riparian corridor with no foraging habitat).

The presence of two small Koala populations known from Kooraban National Park and surrounding contiguous areas and the presence of important food tree species reported from DECC (2010) suggests that essential habitat features are present and the study area may occur in an important corridor for dispersal of Koalas to currently unoccupied habitats to the east of Kooraban, within Gulaga and surrounding areas. Therefore as a precautionary measure, the habitat to be cleared is considered important for local Koala populations in the Dignams Creek area.

The link between Kooraban and Gulaga National Park is relatively narrow in the landscape and is currently intersected by the highway. The results of surveys for this investigation and previous investigations conducted by DECC (2009) and Allen (2011) indicate that Koalas occur in low densities in Kooraban National Park several kilometres west and north west of the highway although are not known from the habitat adjacent to the highway.

The importance of this habitat as a movement and dispersal corridor has been noted in the design and inclusion of three targeted underpass structures comprising one structure in Stage 1 and two structures in Stage 2 linking the two national park areas. This would be a substantial improvement on the current barrier effect of the highway once completed and ensure that the habitat would not become isolated and maintain movements for Koalas.




There is a r ecovery plan for the Koala. Considering the impact is restricted to secondary habitat (class B and C) and there is no evidence of Koala activity in the study area and the inclusion of the proposed mitigation measures to minimise habitat removal and facilitate the natural movements of Koala across the proposal corridor, the proposal is consistent with the objectives of the recovery plan where relevant to the proposal. The footprint has been planned to minimise removal of habitat and therefore consistent with the recovery plan objectives. The objectives of the recovery plan are discussed below:

Recovery Plan Objective Relevance to proposal

Objective 1: To conserve Koalas in their existing habitat.

Habitat removal has been minimised where possible through planning and refinement of the proposal footprint in the areas of identified potential Koala habitat and the proposal potentially contributes to the conservation of Koala through facilitating safe

220


Recovery Plan Objective Relevance to proposal

passage across the highway.

Objective 2: To rehabilitate and restore Koala habitat and populations.

Koala feed trees would be included in any offset plantings and strategic revegetation for the proposal.

Objective 3: To develop a better understanding of the conservation biology of Koalas.

n/a

Objective 4: To ensure that the community has access to factual information about the distribution, conservation and management of Koalas at a national, state and local scale.

n/a

Objective 5: To manage captive, sick or injured Koalas and or phaned wild Koalas to ensure consistent and high standards of care.

n/a

Objective 6: To manage over-browsing to prevent both Koala starvation and ecosystem damage in discrete patches of habitat.

n/a

Objective 7: To coordinate, promote the implementation, and monitor the effectiveness of the NSW Koala Recovery Plan across NSW.

n/a




DIRECT IMPACT


clearing where possible and minimise potential impacts to Koala habitat.


221


Threatening Process Potential impacts, and proposed avoidance and mitigation measures Landscaping would include known feed tree species for Koalas.

















INDIRECT IMPACT









There is some evidence of foxes preying on bandicoots at purpose built fauna underpasses that were placed in disturbed habitats (Harris et al.

222



2010). However, these authors consider this is less likely where multiple Predation and hy bridisation of feral structures are used, as is proposed, possibly minimising the potential for dogs (Canis lupus familiaris) predation. The proposed upgrade includes a c ombination of wildlife

Predation by the European red fox crossing structures, which would include a bridge structure and four fauna (Vulpes vulpes) underpasses.





managing populations of these species. A flora and fauna management by feral goats (Capra hircus)

plan would be developed as part of the CEMP which provides specific Herbivory and env ironmental details for the re-establishment of native vegetation on batters, cut faces, degradation caused by feral deer surrounding sediment basins and other areas disturbed during

construction.

Conclusion

The proposal would remove a relatively small area (19.9 hectares) of secondary class B and C habitat for Koalas. This is considered a m inor loss of potential habitat in this locality given the presence of over 6,000 hectares of similar forests across these two reserves, further the proposed inclusion of targeted crossing structures for Koalas would improve the existing poor connectivity between the reserves effectively providing a positive outcome. The assessment concludes that the proposal is unlikely to lead to a s ignificant impact on local Koala populations and a n SIS is not required.

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Long-nosed Potoroo

The Long-nosed Potoroo is listed as vulnerable in NSW under the TSC Act. In NSW it is generally restricted to coastal heaths and f orests east of the Great Dividing Range, with an annual rainfall exceeding 760 mm. The potoroo inhabits coastal heaths and dry and wet sclerophyll forests. Dense understorey with occasional open areas is an es sential part of habitat, and m ay consist of grass-trees, sedges, ferns or heath, or of low shrubs of tea-trees or melaleucas. A sandy loam soil is also a common feature.

The fruit-bodies of hypogeous (underground-fruiting) fungi are a large component of the diet of the Long-nosed Potoroo. They also eat roots, tubers, insects and t heir larvae and other soft-bodied animals in the soil. Often digs small holes in the ground in a similar way to bandicoots.

Mainly nocturnal, hiding by day in dense vegetation - however, during the winter months animals may forage during daylight hours. Individuals are mainly solitary, non-territorial and have home range sizes ranging between two to five hectares. Breeding peaks typically occur in late winter to early summer and a single young is born per litter. Adults are capable of two reproductive bouts per annum


The species presence was not confirmed in the study area although is considered to have potential to occur. Conical diggings were noted in several locations however these are not distinguishable from the Long-nosed Bandicoot which was observed. The northern end of the proposal corridor, north of Dignams Creek provides suitable habitat for the species given that the soil type and dense understorey compared to the remainder of the study area. Based on known habitat preferences, habitats in the national park areas of the southern section would be c onsidered marginal for this species.

If present, the impacts on this species are likely to be minimal particularly as much of the habitat is marginal and c omparably habitats are well represented through the reserves and within private lands and state forests of the region.


n/a




224


n/a





The habitat to be removed may be considered important in the landscape as part of a key movement corridor between Kooraban and Gulaga National Park.

The importance of this habitat as a movement and dispersal corridor has been noted in the design and inclusion of targeted underpass structures linking the two national park areas. This would be an improvement on the current barrier effect of the highway in this location and ensure that the habitat would not become isolated and maintain movements for this species.




The Office of Environment and Heritage has identified 19 priority actions to help recover the Long-nosed Potoroo in New South Wales. There are no recognised key habitats or populations for this species in the study area and none of these actions are relevant to the proposal or study area. The proposed flora and fauna management plan to be developed as part of the CEMP would ensure that further threats to adjacent potential habitats do not occur.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat resilience, habitat degradation from feral herbivores and increased predation from feral predators.

225



DIRECT IMPACT

Clearing of native vegetation

INDIRECT IMPACT






The proposal would result in the removal of approximately 16.4 hectares of native vegetation considered potential for this species. Proposed avoidance and mitigation measures include: The proposed upgrade has been de signed to minimise vegetation

clearing where possible and minimise potential impacts to fauna habitat.

















226














construction.

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Conclusion

The species presence was not confirmed in the study area although is considered to have potential to occur. Conical diggings were noted in several locations however these are not distinguishable from the Long-nosed Bandicoot which was observed. The northern end of the proposal corridor, north of Dignams Creek provides suitable habitat for the species given that the soil type and dense understorey compared to the remainder of the study area. Based on known habitat preferences, habitats in the national park areas of the southern section would be c onsidered marginal for this species.

If present, the impacts on this species are likely to be minimal particularly as much of the habitat is marginal and c omparably habitats are well represented through the reserves and within private lands and state forests of the region. This factor, in addition to the proposed inclusion of targeted underpass structures suggests that the proposal is unlikely to have a significant impact on the Long-nosed Potoroo and an SIS is not required.

228


Grey-headed Flying-fox

The Grey-headed flying-fox is listed as vulnerable in NSW under the TSC Act. The Grey-headed Flying-fox is Australia's only endemic flying-fox and occurs in the coastal belt from Rockhampton in central Queensland to Melbourne in Victoria (Tidemann 1998). However, only a small proportion of this range is used at any one time, as the species selectively forages where food is available. As a result, patterns of occurrence and r elative abundance within its distribution vary widely between seasons and between years. At a l ocal scale, the species is generally present intermittently and irregularly (Eby & Lunney 2002). At a regional scale, broad trends in the distribution of plants with similar flowering and fruiting times support regular annual cycles of migration (Eby & Lunney 2002).

The species is widespread throughout its range in summer, whilst in autumn it occupies coastal lowlands and is uncommon inland. In winter, the species congregates in coastal lowlands north of the Hunter Valley and is occasionally found on the south coast of NSW associated with flowering Spotted Gum (Corymbia maculata) and on the northwest slopes generally associated with flowering White Box (Eucalyptus albens) or Mugga Ironbark (Eucalyptus sideroxylon) (NSW DECCW 2010).

The national population of the Grey-headed Flying-fox is spatially structured into colonies (Parry-Jones & Wardle 2004). However, there are no separate or distinct populations due to the constant genetic exchange and movement between camps throughout the species' entire geographic range. This indicates that there is one s ingle interbreeding population (Webb & Tidemann 1995; DSE 2005).

The Grey-headed Flying-fox is a canopy-feeding frugivore and nectarivore, which utilises vegetation communities including rainforests, open f orests, closed and open woodlands, Melaleuca swamps and Banksia woodlands. It also feeds on commercial fruit crops and on introduced tree species in urban areas. The primary food source is blossom from Eucalyptus and related genera but in some areas it also utilises a wide range of rainforest fruits (Eby 1998). None of the vegetation communities used by the Grey-headed Flying-fox produce continuous foraging resources throughout the year. As a result, the species has adopted complex migration traits in response to ephemeral and patchy food resources (Eby 1996, 1998; Nelson 1965).

Flying foxes roost communally in open canopy vegetation and the location of day roosts or camps is generally stable through time (Eby 2002). Flying fox camps serve a num ber of functions for the animals including resting habitat within suitable commuting distance of feeding areas which is typically within 20 kilometres but as far as 50 k ilometres (Eby 1996), they are sites of behaviours associated with reproduction and maternal care and they provide refuge at night for flightless young who remain in camps for many weeks while adults feed during the night (Nelson 1965).


The proposal would involve the removal of approximately 20 hectares of potential foraging habitat for the Grey-headed Flying-fox. This is a small proportion of the remaining areas of Kooraban and Gulaga National Park and the surrounding landscape of reserves and state forests in the region.

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Foraging resources for the Grey-headed Flying-fox occur throughout all naturally vegetated areas of the study area and it is likely that the vegetation to be cleared provides a por tion of the foraging range of local populations of Grey-headed Flying-foxes. The projected removal of 20 hec tares is considered a sustainable loss of potential foraging habitat in the context of available habitat in the surrounding region, including several state forests and conservation reserves and considering the broad foraging requirements of the species. The proposed action would not result in a decrease in the size of a local population and would not impact on a known roost site.

Life-cycle characteristics of the species at threat from habitat clearing relate to the loss of critical foraging habitat within a 50 kilometre radius of known camps (DECCW 2009). This is the expected maximum foraging distance of the species from a roost site (Eby 1996).

Given the absence of a r oost camp in the proposal study area, the impacts of construction and operation of the proposal relate to loss of feeding habitat caused by 1) direct clearing or damage to native vegetation during the construction phase and 2) edge effects during operation related to degradation of habitat at the interface with cleared land and altered feeding behaviours of flying-foxes.

The affected area of foraging habitat would represent a small percentage of the total extent of these vegetation types within a 50 kilometre radius of the proposal study area. Similarly, vegetation types containing known diet species as dominants or subdominants are widespread in the study area and the overall impact of loss of these species would be ameliorated by their prevalence in a br oad range of vegetation types such that this proposal is unlikely to lead to a long-term decrease in the size of the population.

(b) In the case of an endangered population, whether the action proposed is likely to have an adverse effect on the life cycle of the species that constitutes the endangered population such that a viable local population of the species is likely to be placed at risk of extinction

n/a




n/a




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The proposal would involve the removal of approximately 20 hectares of potential foraging habitat. Grey-headed Flying-foxes are highly mobile and can readily cross cleared areas such as broad road corridors, and no new-edges would be created and no areas of habitat would become isolated.

Given the absence of a r oost camp in the proposal study area, the impacts of construction and operation of the proposal relate to loss of feeding habitat caused by 1) direct clearing or damage to native vegetation during the construction phase and 2) edge effects during operation related to degradation of habitat at the interface with cleared land and altered feeding behaviours of flying foxes.

The affected area of foraging habitat is likely to represent marginal habitat, with preferred habitat mainly comprising more fertile floodplain areas. The potential impact represents a small percentage of the total extent of these vegetation types within a 50 kilometre radius of the proposal area, with surrounding habitat on more fertile soils likely to be support higher quality foraging habitat. Considering the small proportion of habitat being impacted relative to available habitats in the locality, the relatively marginal nature of the foraging habitats being impacted, no evidence for the presence of a Flying-fox camp within 50 kilometres of the proposal area, and lack of local records (OEH 2012) the habitat potentially being impacted is unlikely to be important for the long-term survival of the species.




There is a nat ional recovery plan for the Grey-headed Flying-Fox. Considering the low potential impact to habitat for this species the proposal is consistent with the objectives of the recovery plan.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of foraging habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat resilience and habitat degradation from feral herbivores. It is considered unlikely that the proposal would increase the likelihood of predation on this species by feral carnivores.

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DIRECT IMPACT


Clearing of native vegetation The proposal would result in the removal of approximately 20 hectares of potential foraging habitat. Proposed avoidance and mitigation measures include: The proposed upgrade has been de signed to minimise vegetation

clearing where possible and minimise potential impacts to habitat.


INDIRECT IMPACT





















Communication strategies to improve contractor awareness of weeds

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and weed management.


The clearing of vegetation may increase the value of the habitat for rabbits (Oryctolagus cuniculus), feral deer (Family Cervidae) and feral goats (Capra hircus) in the study area over the long-term. Revegetation of disturbed areas particularly formerly vegetated sites would assist in managing populations of these species. A flora and fauna management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction.


Herbivory and environmental degradation caused by feral deer

Conclusion

Considering there are no known records of this species (OEH 2012) or roost camps within the proposal locality, and the extensive areas of habitat surrounding the proposal footprint, the habitats potentially impacted by the proposal are unlikely to constitute a significant impact for this species.

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Square-tailed Kite

The Square-tailed Kite is listed as vulnerable in NSW under the TSC Act. The Square-tailed Kite is found in a variety of timbered habitats including dry woodlands and open forests showing a particular preference for timbered watercourses. It is a s pecialist hunter of passerines, especially honeyeaters, and most particularly nestlings, and insects in the tree canopy, picking most prey items from the outer foliage. The species appears to occupy large hunting ranges of more than 100km2. Breeding is from July to February, with nest sites generally located along or near watercourses, in a fork or on large horizontal limbs


There are a number of records in the south coast region and the species could potential hunt and perch in all habitat types identified in the study area. The habitat resource survey was conducted along the entire length of the proposal footprint and at that time no large raptor nests were noted to occur. Any impact from the proposal on this species would be through a temporary disturbance to habitat for prey species rather than nesting or perching areas. This impact is minor and only short-term and not expected to place local populations at risk of extinction.


n/a




n/a





There are a number of records in the south coast region and the species could potentially hunt and perch in all habitat types identified in the study area and therefore up to 25 hectares of remnant vegetation would be removed representing potential habitat for prey species. No nesting was noted

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at the time of the survey and the habitat to be impacted does not present a unique or important area of habitat for this species, particularly in relation to large expanses of comparably habitat throughout the reserves, state forests and private lands in the locality.

At present the potential areas of habitat for this species are bisected by the existing highway and this proposal would contribute to fragmenting habitat. However this is unlikely to impact on this wide-ranging and highly mobile species.




The Office of Environment and Heritage has identified 3 priority actions to help recover the Square-tailed Kite in New South Wales.

Ensure implementation of management strategies that reduce disturbance of riparian areas.

Identify and protect nest trees, and monitor reproduction.

Liaise with local field ornithologist to obtain data on the Square-tailed Kite in the area.

The proposal would include the construction of a flora and fauna management plan as part of the CEMP. The plan would target protection and revegetation of disturbed areas of the waterway crossing during construction and operation. Pre-clearance surveys would be c onducted to identify important features such as large raptor nests to reduce the impact on nesting birds.




DIRECT IMPACT


clearing where possible and minimise potential impacts to fauna

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INDIRECT IMPACT






habitat.

Includes revegetation of obsolete sections of the existing highway.



















There is some evidence of foxes preying on bandicoots at purpose built competition and disease transmission

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by feral pigs (Sus scrofa) fauna underpasses that were placed in disturbed habitats (Harris et al. 2010). However, these authors consider this is less likely where multiple








construction.

Conclusion

A flora and fauna management plan would be prepared as part of the construction environmental management plan (CEMP). It would be prepared in accordance with the RMS Biodiversity Guidelines: Protecting and managing biodiversity on RTA projects (RTA 2011) (Biodiversity Guidelines). The plan would include a c learing procedure, which in turn would specify the requirements for pre-clearing. Pre-clearing surveys would be undertaken by an experienced ecologist to identify and mark the location and extent of important habitats in the construction footprint to be avoided during construction such as bird nests. Any impact from the proposal on the Square-tailed Kite would be through a temporary disturbance to habitat for prey species rather than nesting or perching areas. This impact is minor and only short-term and considered unlikely to have a significant impact on the Square-tailed Kite and a SIS is not required.

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Gang-gang Cockatoo

The Gang-Gang Cockatoo is listed as vulnerable in NSW under the TSC Act. The Gang-gang Cockatoo is distributed from southern Victoria through south- and central-eastern New South Wales. In New South Wales, the Gang-gang Cockatoo is distributed from the south-east coast to the Hunter region, and inland to the Central Tablelands and south-west slopes. It occurs regularly in the Australian Capital Territory. It is rare at the extremities of its range, with isolated records known from as far north as Coffs Harbour and as far west as Mudgee (OEH 2012).

In summer this species is generally found in tall mountain forests and woodlands, and may occur at lower altitudes in winter in drier more open eucalypt forests and woodlands, with old growth habitats being favoured for nesting and roosting (OEH 2012).


An individual was observed and heard calling at the far northern end of the proposal, several hundred metres to the west of the existing highway.

The proposal would result in the removal of approximately 20 hectares of potential foraging habitat with tree hollows potentially suitable as nesting habitat present but observed to be i n very low density. Similar potential habitats in the locality are extensive through private lands, conservation reserves and state forests. There is potential for the life-cycle of the species to be impacted during the breeding season if found to be utilising hollow trees in the proposal area, however mitigation measures including pre-clearance surveys would ensure these impacts are avoided where possible.


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The proposal would result in the removal of approximately 20 hectares of foraging habitat. This species requires large tree hollow cavities for nesting. Based on observations of hollow trees in the study area, large tree hollows are very limited particularly in roadside areas. However the density of all hollows reported in the proposal corridor was also found to be similar across other areas of habitat outside the proposal corridor.

No areas of habitat would become isolated for this species from the clearing activities as this species can readily fly across fragmented habitats including major roads and therefore the proposal would not create a m ajor barrier to this species. The proposal is unlikely to place the species at further risk of vehicle strike considering the grade and elevations of the proposal would be similar to existing conditions.

Habitats in the proposal footprint potentially have some importance for the local population for foraging and potentially for shelter, however relative to the extent of habitat in the locality the impacts represent a small proportion of the available habitat for the local population. Therefore the habitat impacted by the proposal is considered unlikely to be highly important to the species.




There is no recovery plan for this species. There are 11 priority action statements for this species related to scientific research, community awareness, habitat restoration and protection of this species. Considering the low potential impact to habitat to this species and the proposed mitigation measures to minimise habitat removal and restore foraging habitat through the re-establishment of native vegetation including potential feed trees (Eucalyptus spp.), the proposal is consistent with these priority actions.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of foraging, nesting and roosting habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality, increased competition with feral honey bees for hollow resources and habitat degradation from feral herbivores. It is considered unlikely that the proposal would increase the likelihood of predation on this species by feral carnivores.

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DIRECT IMPACT

Clearing of native vegetation

Loss of hollow-bearing trees

Removal of dead wood and dead trees

INDIRECT IMPACT






The proposal would result in the removal of approximately 7.4 hectares of native vegetation supporting hollow-bearing trees, dead wood and dead trees. Proposed avoidance and mitigation measures include: The proposed upgrade has been de signed to minimise vegetation

clearing where possible and minimise potential impacts to threatened species habitat.

















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Competition from feral honey bees (Apis mellifera)

While the proposal would not directly increase bee numbers, the removal of hollow-bearing trees would indirectly increase competition for hollows by native fauna because the loss of tree hollows via occupation by feral honeybees reduces the number of hollows available for native animals to breed and shelter.





Conclusion

The proposal would result in the removal of approximately 20 hectares of potential foraging habitat with tree hollows potentially suitable as nesting habitat. Similar potential habitats in the locality are extensive through private lands, conservation reserves and state forests. There is potential for the life-cycle of the Gang-Gang Cockatoo to be impacted during the breeding season if found to be utilising hollow trees in the proposal area, however mitigation measures including pre-clearance surveys would ensure these impacts are avoided where possible. The proposal is considered unlikely to impose a significant impact on the Gang-Gang Cockatoo and a SIS is not required.

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Glossy Black-cockatoo

The Glossy Black-cockatoo is listed as vulnerable in NSW under the TSC Act. The Glossy Black-cockatoo occupies forests of south-eastern Australia, from Shoalwater Bay in central Queensland to the Victorian border region. Isolated populations also exist in the Eungella district of Queensland and on Kangaroo Island, South Australia.

The Glossy Black-cockatoo is considered rare in the national context (Garnett 1992) but moderately common in New South Wales (Morris et al 1981), Blakers et al (1984) suggests the species is as widely distributed now as in the recent past but dependence on one type of food makes it vulnerable. The Glossy Black-cockatoo relies almost entirely on the seeds of a few species of She-oak for food and any factor that reduces the quantity, quality or availability of the seed crop of these trees must have a direct impact on local populations, through starvation or reduced fecundity. Land clearance for agriculture has substantially reduced available habitat and the species is likely to be sensitive to continued habitat destruction in the future. Regular fire may also reduce the presence of fruiting She-oaks. The bird is also dependent upon large cavities in mature eucalypts for nesting. The destruction of hollows through timber removal, apiary practices and fire may also adversely affect populations.

Habitat for this species generally consists of moist and dry eucalypt forest types with a S he-oak understorey. Glossy Black-cockatoos require hollows for nesting and She-oak fruit, on which it usually feeds in small groups. This species roosts communally at night, travelling at dawn to groves of seeding She-oaks to spend the day feeding. The birds are very quiet when feeding and can be easily approached. Their feeding method is highly ritualised, with the cone being held in the left foot whilst being fragmented by the specialised bill. In areas where She-oaks are abundant, this species is sedentary, however, in other areas; Glossy Black-cockatoos can be no madic, moving between food sources.

The breeding season is between March and August with eggs usually being laid between April and June. The nests are located in hollow limbs or trunks, often in tall dead trees standing in clearings. The nests are usually between 13 and 22 metres above the ground. A single egg is laid and the male visits the brooding female at dusk, calling to her. Both male and female fly to a nearby tree where the male feeds the female. I ncubation takes approximately four weeks and the young are fledged at around 9 - 10 weeks (Australian Museum Business Services 1995).


The proposal would result in the removal of approximately 16.4 hectares of forested habitat containing suitable foraging resources of which only a small proportion supports suitable feed tree species (Allocasuarina littoralis). Allocasuarina spp. were not observed in the remaining 6 hectares to be removed by the proposal. Successful breeding requires feed trees, nesting trees and water to be located together, and hollow trees in the study area are potentially suitable as nesting habitat. Records of this species from the field surveys were to the east and west of the existing highway,

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several hundred metres from the proposal indicating that the habitat for local populations is widespread.

The potential habitats in the locality are extensive and associated with Kooraban and Gulaga National Park but also extensive other areas of private land, reserves and state forests. Considering the small proportion of habitat being impacted in the proposal area relative to the available habitat in the locality a viable local population of this species is unlikely to be placed at risk of extinction.


n/a




n/a





The proposal would result in the removal of approximately 16.4 hectares of foraging habitat of which only a small proportion supports suitable feed tree species (Allocasuarina littoralis). Feed trees species are not concentrated in the proposal footprint and exist only as scattered individuals. No evidence of foraging was identified, as shown by the presence of chewed cones. Foraging activity was noted in private lands adjoining Gulaga National Park on the ridge to the east of the highway corridor. While some use of the corridor could be expected it is evident that foraging activity by this species is widespread.

The vegetation clearing would not result in areas of habitat becoming isolated for this species. This species can readily fly across fragmented habitats including major roads, and therefore the proposal is unlikely to create a major barrier to this species. Habitats in the proposal footprint potentially has some importance for the local population for foraging and for nesting, however relative to the extent of habitat in the locality the removal of this habitat represents a s mall proportion of the available habitat for the local population. Therefore the habitat impacted by the proposal is considered unlikely to be highly important to the species.

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There is no recovery plan for this species. There are 10 priority action statements for this species related to scientific research, community awareness, habitat restoration and protection of this species. Considering the low potential impact to habitat to this species and the proposed mitigation measures to minimise habitat removal and restored foraging habitat (feed trees), the proposal is consistent with these priority actions.


Key threatening processes that are relevant to this species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be m itigated by the proposal. The main key threatening processes relevant to this species that are directly enacted by the proposal are those associated with clearance and degradation of foraging, nesting and roosting habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality, increased competition with feral honey bees for hollow resources and habitat degradation from feral herbivores. It is considered unlikely that the proposal would increase the likelihood of predation on this species by feral carnivores.


DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 7.4 hectares of native vegetation supporting hollow-bearing trees, dead wood and dead

Loss of hollow-bearing trees trees, and bushrock. Proposed avoidance and mitigation measures Removal of dead wood and dead include: trees The proposed upgrade has been de signed to minimise vegetation



INDIRECT IMPACT



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A nest box management strategy would be d eveloped as part of the CEMP. The nest box management plan would detail ongoing monitoring and maintenance requirements including the removal of feral honey bees.

The clearing of vegetation may increase the value of the habitat for rabbits (Oryctolagus cuniculus), feral deer (Family Cervidae) and feral goats (Capra hircus) in the study area over the long-term. Revegetation of disturbed areas particularly formerly vegetated sites would assist in managing populations of these species. A flora and fauna management

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plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction.

Conclusion

Based on the field evidence of the Glossy Black-cockatoo which shows foraging activity over a wide area and a lso considering the small proportion of food resources that would be r emoved the proposal is unlikely to constitute a significant impact to the Glossy Black-cockatoo and a SIS is not required.

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Pink Robin

The Pink Robin is listed as vulnerable in NSW under the TSC Act. The Pink Robin inhabits rainforest and tall, open eucalypt forest, particularly in densely vegetated gullies. Catches prey by the perch-and-pounce method, foraging more on the ground than the more flycatcher-like Rose Robin. Insects and spiders are the main dietary items. Breeds between October and January and can produce two clutches in a season. The nest is a deep, spherical cup made of green moss bound with cobweb and adorned with camouflaging lichen, and is lined with fur and plant down. It is situated in an upright or oblique fork, from 30cm to 6m above the ground, in deep undergrowth.

Females do most or all of the nest building and incubate unaided, but both adults feed the nestlings. The most common call most closely resembles a snapping twig


Suitable habitat is marginal is some of the wetter gullies, particularly to the north of Dignams Creek on the western side of the highway and at the far southern end of the proposal on the eastern side of the highway there is a small area of potential habitat just outside the proposal footprint. The impacts to potential habitat would equate to less than 4 hectares.

The majority of the study area is open forests and slopes that are unsuitable for this vagrant species during the breeding season. However this species is known to migrate to more open habitats during winter and the study area appears to be more suited as wintering (non-breeding) habitat.

The proposal would remove a small area of habitat for prey species, mostly insects and spiders but would not impact on the breeding life-cycle.


n/a




n/a



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The Pink Robin inhabits rainforest and tall, open eucalypt forest, particularly in densely vegetated gullies. Suitable habitat is marginal is some of the wetter gullies, particularly to the north of Dignams Creek on the western side of the highway and at the far southern end of the proposal on the eastern side of the highway there is a small area of potential habitat just outside the proposal footprint.

The impacts to potential habitat would equate to less than 4 hectares of habitat for prey species and would contribute to fragmentation of habitat in the study area for very small bird species. However the longer distance migratory behaviour of this species suggests that it is adapted to moving across fragmented landscapes.

There would be no impact on breeding habitat and the study area would not be considered important for the species.




The Office of Environment and Heritage has identified 4 priority actions to help recover the Pink Robin in New South Wales.

Using current records and literature on habitat requirements determine the current distribution and identify areas of potential habitat to undertake survey and management actions.

Determine, through research, the ecological requirements of the species, particularly in regard to fire, and incorporate the information into Regional and Local Fire Plans.

Use management agreements and incentives on private and leasehold land to manage total grazing pressure through such actions as removal of artificial water points and feral and native herbivore control.

Review existing forestry operations in wet sclerophyll forest on S FNSW and p rivate land to determine overall impact on the value of habitat for this species, amend licensing prescriptions if necessary and/or identify areas where no harvesting would occur

The study area is not recognized as a key area or known population and these actions to not apply to the proposal.


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DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 16.4 hectares of native vegetation supporting suitable habitat for this species.

INDIRECT IMPACT







vehicles and f ootwear is free of soil before entering or exiting the site.

The risk of spreading pathogens and the mitigation measures required on site would be r egularly communicated to staff and contractors during inductions and toolbox talks.










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A flora and fauna management plan would be developed as part of the competition and disease transmission CEMP which provides specific details for the re-establishment of native by feral pigs (Sus scrofa) vegetation surrounding fauna crossing structures with the aim of

Predation and hy bridisation of feral minimising the potential for predation. dogs (Canis lupus familiaris)

Woody debris and b ushrock would be r e-used on s ite for habitat Predation by the European red fox improvement where applicable and would be detailed in CEMP. Suitable (Vulpes vulpes) areas for re-use include the approaches to fauna underpasses, beneath

the proposed bridge structure and would aim to minimise the potential for predation through providing cover for native fauna.





construction.

Conclusion

The majority of the study area is open forests and slopes that are unsuitable for the Pink Robin during the breeding season. However this species is known to migrate to more open habitats during winter and the study area appears to be more suited as wintering (non-breeding) habitat.

The proposal would remove a s mall area of habitat for prey species but would not impact on the breeding life-cycle or lead to local extinction. The proposal is considered unlikely to lead to a significant impact on the Pink Robin and a SIS is not required.

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Giant Burrowing Frog

The Giant Burrowing Frog is listed as vulnerable in NSW under the TSC Act. The species is found in heath, woodland and open dry sclerophyll forest on a variety of soil types except those that are clay based. The Giant Burrowing Frog spends more than 95 per cent of its time in non-breeding habitat in areas up to 300 metres from breeding sites. Whilst in non-breeding habitat it burrows below the soil surface or in the leaf litter. Individual frogs occupy a series of burrow sites, some of which are used repeatedly. The home ranges of both sexes appear to be non-overlapping suggesting exclusivity of non-breeding habitat. Home ranges are approximately 0.04 hectares in size. Breeding habitat of this species is generally soaks or pools within first or second order streams. They are also commonly recorded from 'hanging swamp' seepage lines and where small pools form from the collected water


Potential habitat was noted along Blinds Creek which is a tributary of Dignams Creek and also the upper reaches of Dignams Creek outside of the study area are also suitable. The lower portions of Dignams Creek impacted by the proposal appear to be too deep and rapid flowing to be suited as breeding sites for this species and are considered only very marginal. Breeding habitat of this species is generally soaks or pools within first or second order streams. They are also commonly recorded from 'hanging swamp' seepage lines and where small pools form from the collected water. As such the areas of potential breeding habitat noted are outside of the proposed proposal footprint and upstream of the activity outside of the potential zone of disturbance.

Some areas of non-breeding habitat near Blinds Creek may be impacted particularly on the south-side of Dignams Creek Road in loamy and sandy soils. The impact area would equate to less than 2-3 hectares.


n/a




n/a



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The areas of potential breeding habitat noted are outside of the proposed proposal footprint and upstream of the activity outside of the potential zone of disturbance. Some areas of non-breeding habitat near Blinds Creek may be impacted particularly on the south-side of Dignams Creek Road in loamy and sandy soils. The impact area would equate to less than 2-3 hectares.

The clearing for the proposal would not isolate areas of breeding or non-breeding habitat which would be retained outside of the construction zone. Important breeding areas of habitat may occur within the region in the upper reaches of the Dignams and B lind Creek ecosystems, however not within the proposal area.




The Office of Environment and Heritage has identified 20 priority actions to help recover the Giant Burrowing Frog in New South Wales. Of these the only one relevant to the proposal would be the protection of known sites. While the species has not been confirmed in the study area, potential habitat has been identified. The proposal would not directly impact on t hese areas of potential breeding habitat that may be considered important.




DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 0.18 hectares of native riparian vegetation. Proposed avoidance and mitigation measures include: The proposed upgrade has been designed to minimise vegetation

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Threatening Process

clearing where possible.


INDIRECT IMPACT

Infection of native plants by At this point there is no evidence of pathogens in the study area. If there is Phytophthora cinnamomi potential for equipment and personnel to introduce pathogens to the area

during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA 2011) would be implemented. These include: The provision of vehicle and boot wash down facilities and ensure

Infection of frogs by amphibian vehicles and footwear is free of soil before entering or exiting the site. chytrid causing the disease

The risk of spreading pathogens and the mitigation measures required on chytridiomycosis site would be regularly communicated to staff and contractors during

inductions and toolbox talks.

Construction works would be programmed to move from uninfected areas Introduction and Establishment to any known infected areas. of Exotic Rust Fungi of the order

Pucciniales pathogenic on Restriction of vehicles to designated tracks, trails and parking areas. plants of the family Myrtaceae If required the above pathogen management measures would be implemented

throughout the entire construction period.

Invasion of native plant Weed species are prevalent in disturbed habitats of the study area including communities by exotic perennial roadside environments and cleared paddocks. A weed management plan grasses would be developed as part of the CEMP. The details of the weed

management plan would vary for each site but would include: Invasion and establishment of Taxa and potential sources of the weed species. exotic vines and scramblers

Weed management priorities and objectives. Invasion and establishment of Sensitive environmental areas within or adjacent to the site. Scotch broom (Cytisus

Location of weed infested areas. scoparius)







Predation by the feral cat (Felis The proposal may contribute to increased levels of predation on native fauna catus) from foxes, wild dogs, pigs and cats, through the impact of habitat removal

leading to displacement of resident fauna. Predation, habitat degradation,

There is some evidence of foxes preying on bandicoots at purpose built fauna competition and disease underpasses that were placed in disturbed habitats (Harris et al. 2010). transmission by feral pigs (Sus


253



scrofa) However, these authors consider this is less likely where multiple structures are used, as is proposed, possibly minimising the potential for predation. The

Predation and hybridisation of proposed upgrade includes a combination of wildlife crossing structures, which feral dogs (Canis lupus would include a bridge structure and four fauna underpasses. familiaris) A flora and fauna management plan would be developed as part of the CEMP Predation by the European red which provides specific details for the re-establishment of native vegetation fox (Vulpes vulpes) surrounding fauna crossing structures with the aim of minimising the potential

for predation.

Woody debris and bushrock would be re-used on site for habitat improvement where applicable and would be detailed in CEMP. Suitable areas for re-use include the approaches to fauna underpasses, beneath the proposed bridge structure and would aim to minimise the potential for predation through providing cover for native fauna, and excluding potential feral predators.

Competition and grazing by the The clearing of vegetation may increase the value of the habitat for rabbits feral European rabbit (Oryctolagus cuniculus), feral deer (Family Cervidae) and feral goats (Capra (Oryctolagus cuniculus) hircus) in the study area over the long-term. Revegetation of disturbed areas

particularly formerly vegetated sites would assist in managing populations of Competition and habitat

these species. A flora and fauna management plan would be developed as degradation by feral goats

part of the CEMP which provides specific details for the re-establishment of (Capra hircus)

native vegetation on batters, cut faces, surrounding sediment basins and other Herbivory and environmental areas disturbed during construction. degradation caused by feral deer

Conclusion

The areas of potential breeding habitat noted are outside of the proposed proposal footprint and upstream of the activity outside of the zone of disturbance. Some areas of non-breeding habitat near Blinds Creek may be impacted particularly on the south-side of Dignams Creek Road in loamy and sandy soils. The impact area would equate to less than 2-3 hectares and not considered significant for the Giant Burrowing Frog. A SIS is not required.

A number of mitigation measures have been recommended and would be implemented as part of an overall construction environmental management plan (CEMP). Avoidance and mitigation measures that would be implemented to minimise impacts to habitats for Giant Burrowing Frog, including:

Appropriate road design to avoid suitable habitat for amphibians where possible.

As part of the CEMP opportunities to avoid areas of habitat during construction will be investigated and the proposed clearing boundary adjacent to these habitats will be delineated on the ground to avoid accidental incursions into adjacent areas of habitat.

Basic temporary fencing would be installed to indicate the limits of clearing and exclusion zones will be established in areas of habitat outside these clearing limits.

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A weed management plan would be developed as part of the CEMP to limit the spread of weeds to adjacent retained areas of habitat.

Measures to prevent the introduction and/or spread of pests and disease causing agents such as chytrid fungus would be incorporated into the CEMP for the proposal.

A landscape management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction including areas of habitat for amphibians.

The bridge structure over Dignams Creek will be designed and managed to minimise any potential impact to flow regimes which may indirectly impact habitat for amphibians.

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Stuttering Frog

The Stuttering Frog is listed as endangered in NSW under the TSC Act. The species is found in rainforest and wet, tall open forest in the foothills and escarpment on the eastern side of the Great Dividing Range. Suitable habitat is widespread in the region particularly to the west of the study area in the more contiguous wet forests along the range and only considered marginal in the study area.

Outside the breeding season adults live in deep leaf litter and thick understorey vegetation on the forest floor. Feed on insects and smaller frogs. Breed in streams during summer after heavy rain. Eggs are laid on rock shelves or shallow riffles in small, flowing streams. As the tadpoles grow they move to deep permanent pools and take approximately 12 months to metamorphose.


If present in the locality the preferred areas of habitat would occur in the upper reaches of Dignams Creek and Blind Creek upstream of the proposal corridor and outside of the zone of influence. The proposal is unlikely to impact on the habitat or life-cycle of the species.


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The species is found in rainforest and wet, tall open forest in the foothills and escarpment on the eastern side of the Great Dividing Range. Suitable habitat is widespread in the region particularly to the west of the study area in the more contiguous wet forests along the range and only considered marginal in the study area.

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The Office of Environment and Heritage has identified 7 priority actions to help recover the Stuttering Frog in New South Wales. Of these the only one relevant to the proposal would be the protection of known sites. While the species has not been confirmed in the study area, potential habitat has been identified. The proposal would not directly impact on these areas of potential breeding habitat that may be considered important.




DIRECT IMPACT

Clearing of native vegetation The proposal would result in the removal of approximately 0.18 hectares of native vegetation in riparian areas. Proposed avoidance and mitigation measures include: The proposed upgrade has been designed to minimise vegetation

clearing where possible.

INDIRECT IMPACT

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Infection of frogs by amphibian chytrid causing the disease chytridiomycosis
























There is some evidence of foxes preying on bandicoots at purpose built fauna underpasses that were placed in disturbed habitats (Harris et al.

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2010). However, these authors consider this is less likely where multiple Predation and hy bridisation of feral structures are used, as is proposed, possibly minimising the potential for dogs (Canis lupus familiaris) predation. The proposed upgrade includes a c ombination of wildlife

Predation by the European red fox crossing structures, which would include a bridge structure and four fauna (Vulpes vulpes) underpasses.







construction.

Conclusion

The small areas of potential breeding habitat for the Stuttering Frog were noted to occur well outside of the proposed proposal footprint and upstream of the activity therefore outside of the potential zone of disturbance. The Stuttering Frog is considered unlikely to be significantly impacted by the proposal and a SIS is not required.

A number of mitigation measures have been recommended and would be implemented as part of an overall construction environmental management plan (CEMP). Avoidance and mitigation measures that would be implemented to minimise impacts to habitats for Stuttering Frog, including:

Appropriate road design to avoid suitable habitat for amphibians where possible.

As part of the CEMP opportunities to avoid areas of habitat during construction will be investigated and the proposed clearing boundary adjacent to these habitats will be delineated on the ground to avoid accidental incursions into adjacent areas of habitat.


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A weed management plan would be developed as part of the CEMP to limit the spread of weeds to adjacent retained areas of habitat.

Measures to prevent the introduction and/or spread of pests and disease causing agents such as chytrid fungus would be incorporated into the CEMP for the proposal.

A landscape management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction including areas of habitat for amphibians.

The bridge structure over Dignams Creek will be designed and managed to minimise any potential impact to flow regimes which may indirectly impact habitat for amphibians.

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Large Forest Owls (Powerful Owl, Barking Owl, Masked Owl and Sooty Owl)

All four large forest owl species are listed as vulnerable in NSW under the TSC Act.

The Barking Owl is generally considered to inhabit open forests, woodlands, dense scrubs, foothills, river red gums, and other large trees near watercourses. T ends to penetrate otherwise open country and also paperbark woodland. The Barking Owl prefers drier and more open habitats than does the Powerful Owl and appears more tolerant of human activity (Debus 1997). Kavanagh et al (1995) suggests that the species is particularly associated with coastal lowland or riparian woodland dominated by various red gum species.

Unlike other large forest owl species, the Barking Owl tends to roost in dense foliage in either eucalypts or non-eucalypts including midstorey shrubs. It also roosts in Rough-barked Apple which generally exhibits a m ore densely foliaged canopy than most eucalypts. T here are records of Barking Owls roosting in Wilga trees (Geijera parviflora, in gully rainforest, and in various introduced trees around farm buildings and ev en in largely urban areas. However in general it appears that roost trees are commonly selected that have denser daytime cover than is usually provided by eucalypts (Debus 1997), although the species is does roost in eucalypts as well.

The diet of the Barking Owl consists of mammals, birds and i nsects the percentage of which depends largely on seasonal availability. For instance insects are more readily taken during the warmer months of the year and vertebrates appear to be m ore important during the post-fledging phase of the breeding cycle when the adults’ owls are still feeding young. Mammal prey consists of mostly arboreal species, particularly the Sugar Glider (Petaurus breviceps). The species is known to prey also on large birds such as galahs, various parrot species including cockatoos, and kookaburras. Dietary records suggest the Barking Owl to be an adaptable and generalised predator that is able to switch to introduced prey species, take more diurnal birds than most Australian owls, and subsist on insects in the warmer post-breeding months (Debus 1997).

Most recorded breeding events of the Barking Owl in NSW have been in live river red gums on riparian woodland of that species. In general, the species nests in large tree-hollows with entrances averaging 2-29 metres above ground, depending on the forest or woodland structure and the canopy height (Debus 1997).

The Barking Owl is threatened with loss of habitat, particularly on flatter topography on and adjacent to floodplains, and changes to the age structure of tree cover, resulting in the decline of old growth and dead trees. O ther threats include the loss and degradation of habitat, including the loss of hunting habitat and potential roosting and nest sites and habitat occupied by its prey base. The major factor is further clearing for agriculture in inland NSW, compounded by suppression of eucalypt regeneration by grazing, decline of remnant trees in cleared areas, and reduction of prey (decline of small native mammals) in woodland remnants.

The Masked Owl is recorded as thinly distributed over much of eastern Australia however the majority of records are located over a broad coastal strip in forest and woodland around southern and eastern Australia. Generally considered to be a bird of forest margins and in this region it has been recorded mostly in drier open forest and woodland habitat types. I t is believed that this species prefers a m ore open vegetative structure than either the Powerful or Sooty Owl. This

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species has been particularly recorded in areas with a diversity of vegetation structural types and/or a mosaic of dense and sparse ground cover (Debus 1993). Debus & Rose (1994) analysed habitat types from confirmed nocturnal records and found that the majority of observations of this species were located within wet and dry forest and woodland, and many of the remainder were made from forest and woodland edge or adjacent open country. This species has been recorded utilising treed urban areas. T he high prevalence of road-kills of this species suggests that it makes use of the edge effect created by roads through wooded habitats (Debus & Rose 1994).

Known threats to this species include the loss of foraging habitat and nest sites (suitable tree hollows). Any activity which reduces the prey of this species has the potential to influence survival rates and breeding fecundity. Road-kills are a par ticular problem in fragmented habitats as the hunting technique makes this species susceptible to collisions with vehicles.

The Masked Owl breeds in a variety of wooded habitats, but most of the recorded nest sites have been within live Eucalypts in open or tall open forest, on average some 17 metres from the ground. Loss of potential and actual nest sites is a significant threat to this species.

Prey items in eastern New South Wales largely consist of small to medium-sized terrestrial mammals (less than 600g), including rats, mice and Rabbits but arboreal mammals such as Sugar Gliders and Common Ringtail Possums, as well as birds, may also be taken. An analysis of diet samples of this species analysed by Debus & Rose (1994) suggests that the majority of predation, by biomass, was of terrestrial species. The Masked Owl has adapted well to forage on introduced species such as Black Rat (Rattus rattus) and Rabbits, particularly within disturbed coastal sites. It is evident that this species opportunistically preys upon the most abundant or available ground mammals (Debus & Rose 1994). Masked Owls apparently make use of the edge effect created by roads through forest and the interface between forest and cleared land when foraging for prey. The Masked Owl is believed to be a s tationary hunter, using a series of regular low perches within its territory to wait for prey, which it locates by sound. Prey appears to be taken in a slow deliberate attack without the need of pursuit (Debus 1993).

The Powerful Owl ranges over a broad coastal and sub-coastal strip in south-eastern Australia, from southern Queensland to western Victoria where it is generally confined to altitudes below 1,500 metres. The majority of records have been located east of the Great Dividing Range however a few recorded observations have been made on the inland slopes. Powerful Owls have been observed to inhabit and br eed in forested areas within major urban centres such as Sydney, Brisbane and Newcastle. Within New South Wales, the majority of records have been located within open forests, but woodland, ecotones with cleared areas, riparian habitats and closed forests are also utilised (Debus & Chafer 1994). This species apparently reaches optimum population densities in gullies in dense, undisturbed mountain eucalypt forest, but is not confined to this habitat (Australian Museum Business Services 1995).

The low annual reproductive rate and dependence upon suitable prey items, which are obtained in an extensive home range, suggests that this species is vulnerable to human pressures arising from reductions in nest sites or prey availability. Furthermore, habitat loss and fragmentation may cause problems for young owls dispersing and successfully finding a mate (Debus & Chafer 1994). Widespread clearance and habitat fragmentation throughout its known range has reduced

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populations in the past. Fire can reduce prey numbers, and inappropriate burning regimes can lead to a simplification in the habitat structure and quality and removing resources used by prey species.

Powerful Owls are sedentary, living either alone or in pairs, and oc cupying a permanent territory which contains a number of roost sites. Pairs occupy permanent mutual territories although they commonly roost separately. Several roosts are used in rotation, several days at a time. A typical roost is on a horizontal limb several metres from the ground, uncluttered laterally but screened from above by dense foliage (Australian Museum Business Services 1995). The bird requires a large home range to obtain sufficient abundance of prey items and the size of the territory appears to be related to the availability of suitable prey items (Blakers et al 1984). Medium-sized arboreal mammals, particularly possums, gliders, and b irds are common prey items. Records suggest that Powerful Owls are more inclined to forage within the tree canopy rather than utilise low perches beside breaks in ground cover (Debus & Chafer 1994).

Breeding records in New South Wales suggest that nesting generally occurs within open forest, in live eucalypts with hollow entrances 9 - 37 metres above the ground. Nest trees typically utilised are emergent, often the largest within a stand and oldest within a forest patch, and pairs are known to breed in the same nest for many years.

The Sooty Owl occurs in tall, wet old-growth forest on f ertile soil with a dense understorey and emergent tall eucalypts. Suitable habitat is largely confined to gullies where the species lives in pairs roosting in the daytime amongst dense vegetation, in tree hollows and sometimes in caves. Nesting is usually in the trunks of tall eucalypts with the same nest being used repeatedly.

The species is known to prey mainly on arboreal mammals with a small proportion of birds and terrestrial mammals also taken, ranging in size from marsupial mice Antechinus and House mouse to Common Ringtail Possums and Sugar Gliders.

Inappropriate forest management represents the current main threat to the Sooty Owl, in particular the disturbance and clearing of creek side rainforest, particularly of nest trees and by clear felling for forestry. The habitat of the Sooty Owl is also vulnerable to fire, either wildfires or prescribed burns that are allowed to burn into the rainforest fringes.

The forest owl species are known to occupy very large territories particularly in fragmented areas, which is a r eflection of their high mobility and diversity of prey species taken. Whilst the subject species are known to occasionally roost by day in dense thickets of vegetation or foliage their nesting requirements are more specialised being totally dependent on s uitably large tree-hollows generally found in the trunks of tall, living, mature trees.

Their dependence on this specific habitat feature restricts the local distribution of the species at least for breeding life-cycle requirements and highlights their vulnerability to increased clearing and fragmentation. Generally foraging territory is more widespread and may occur throughout a variety of habitat types depending on the species, with the Powerful Owl ranging from swamp forest to wet and dry sclerophyll, preferably with wet gullies for roosting and the Barking Owl and Mas ked Owl favouring the more open forest and woodland types for foraging, particularly on the edge of open lands.

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The proposal would result in the removal of approximately 20 hectares of foraging habitat for these species, supporting prey species such as possums and gliders, particularly for the Powerful Owl and Barking Owl. Very large tree hollows potentially suitable as nesting habitat were not identified in the proposal footprint and the survey revealed a lack of large hollows from immediately adjoining areas as well. The potential for nesting in the proposal corridor is considered very low.

Several potential prey species were recorded in the study area including possums, gliders and small terrestrial mammals and both Powerful Owl and Barking Owl are considered the most likely of these species to forage in roadside areas to be removed by the proposal. There is a potential for increased roadkill of forest owls hunting in roadside areas, however considering the grade and elevations of the proposal would be similar to existing conditions the proposal is unlikely to place these species at further risk of vehicle strike.

Potential habitats in the locality are extensive and the small loss of potential foraging habitat on the edge of the highway is not expected to place these species at risk of extinction.


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The proposal would result in the removal of approximately 20 hectares of habitat for prey species for the large forest owl species. Tree hollows potentially suitable as nesting habitat for large forest owls were not recorded in the road corridor and were observed to be in low density throughout the locality generally, however tree hollows suitable for prey species are present and are important to maintain

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prey populations. Me asures to maintain hollow resources potentially lost as part of the proposal include the provision of nest boxes.

Large forest owls can readily fly across fragmented habitats including major roads and therefore the proposal is unlikely to create a major barrier to these species. The proposal is unlikely to place these species at further risk of vehicle strike considering the grade and elevations of the proposal would be similar to existing conditions.

Habitats in the proposal footprint potentially have some importance for the local populations of these species for hunting, however relative to the extent of habitat in the locality the impacts represents a small proportion of the available habitat for the local population. Therefore the habitat impacted by the proposal is considered unlikely to be highly important to these species.




There is a recovery plan for Large Forest Owls. Considering the low potential impact to habitat for this species and the minimisation of habitat removal, the proposal is consistent with the objectives of the recovery plan.


Key threatening processes that are relevant to these species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be mitigated by the proposal. The main key threatening processes relevant to these species that are directly enacted by the proposal are those associated with clearance and degradation of foraging, nesting and roosting habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality, increased competition with feral herbivore and invertebrate pests, and increased predation from feral predators on prey species.


DIRECT IMPACT


Loss of hollow-bearing trees

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trees, and bushrock. Proposed avoidance and mitigation measures Bushrock removal include: The proposed upgrade has been designed to minimise vegetation


A flora and fauna management plan would be developed as part of the Construction Environment Management Plan (CEMP) which

Removal of dead wood and dead provides specific details for the re-establishment of native vegetation trees on batters, cut faces, surrounding sediment basins and other areas

disturbed during construction.

A nest box management strategy would be developed as part of the CEMP. The number and type of nest boxes required would be determined during the pre-clearance surveys based on the number, quality and size of the hollows that would be removed. The nest box management plan would detail the specifications for nest box dimensions, target species, installation requirements, locations of nest boxes and ongoing monitoring and maintenance.

Woody debris and bushrock would be re-used on site for habitat improvement where applicable and would be detailed in the landscape management plan/CEMP. Suitable areas for re-use may include the approaches to fauna underpasses, beneath the proposed bridge structure at Dignams Creek and rehabilitation areas.

INDIRECT IMPACT


area during construction then detailed prevention methods as outlined in the RMS Biodiversity Guidelines – Guide 7 Pathogen Management (RTA 2011) would be implemented. These include: The provision of vehicle and boot wash down facilities and ensure

Introduction and Establishment of vehicles and f ootwear is free of soil before entering or exiting the Exotic Rust Fungi of the order site. Pucciniales pathogenic on plants of

The risk of spreading pathogens and the mitigation measures the family Myrtaceae required on site would be r egularly communicated to staff and

contractors during inductions and toolbox talks.




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A nest box management strategy would be d eveloped as part of the CEMP. The nest box management plan would detail ongoing monitoring and maintenance requirements including the removal of feral honey bees.



Predation and hybridisation of feral dogs (Canis lupus familiaris)




Woody debris and b ushrock would be r e-used on s ite for habitat improvement where applicable and w ould be det ailed in the landscape management plan/CEMP. Suitable areas for re-use include the approaches to fauna underpasses, beneath the proposed bridge structure at Dignams Creek and would aim to minimise the potential for predation through providing cover for native fauna, and excluding potential feral predators.

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Conclusion

Considering the small area of foraging habitat that would be removed relative to the extent of similar habitats in the locality and the absence of suitable nest sites in the proposal area, the proposal is unlikely to constitute a significant impact to large forest owls and a SIS is not required. In addition to avoidance of potential foraging habitat, mitigation measures will be implemented to minimise impacts to potential prey species through the installation of nest boxes. A nest box management strategy would be developed as part of the construction environment management plan.

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Cave-roosting bats (Large-eared Pied Bat, Eastern Bent-wing Bat, and Southern Myotis)

All three species are listed as vulnerable in NSW under the TSC Act. Eastern Bentwing Bat has been recorded during surveys conducted in the study area for this project

Eastern Bent-wing Bat is widespread and can be locally common where suitable caves or tunnels are available as roost sites. However, the major threat to this species is the loss of roost sites, and nursery caves. T he dependence on r elatively few nursery caves suggests that threats to the existence or structural integrity of these may place populations in jeopardy (Dwyer 1995). Frequent disturbance of roosts used for winter hibernation is known to significantly increase winter mortality. Toxic accumulation of agricultural chemicals in body fat used during winter torpor may also reduce populations. Habitat loss through clearing for development or agriculture and subsequent reductions in insect prey availability may also adversely affect this species. T he Eastern Bent-wing Bat is reportedly preyed upon by feral Cats and occasionally Foxes.

Eastern Bent-wing Bats are known to forage within a variety of habitat types adjoining roost sites. This appears to include rainforest, moist and dry eucalypt forest, swamp sclerophyll forest as well as heath. Known roost sites include caves, old mines, stormwater channels, road culverts and comparable structures including buildings. D wyer (1995) regards typical habitat as well-timbered valleys. This species has been reported utilising bushland remnants in urban areas.

Eastern Bent-wing Bats are known to feed on moths, cockroaches, grasshoppers and an ts and forages above the tree canopy (Australian Museum Business Services 1995). This is a mobile species and is estimated to forage within a 20 km radius in a single night.

The limiting factor is the availability of roost sites, with suitable caves, mines, road culverts and occasionally buildings being essential. Lon g migrations between roosts, according to seasonal needs or reproductive status, have been recorded. W ith the onset of spring, adult females move from numerous widely scattered roosts to specific nursery caves, which provide high temperature and humidity or have an internal conformation which retains air warmed by the bats activities (Dwyer 1995). Within nursery caves, the density of young bats can be up to 3 000 per square metre.

The Large-eared pied Bat is found mainly in areas with extensive cliffs and c aves, from Rockhampton in Queensland south to Bungonia in the NSW Southern Highlands. It is generally rare with a very patchy distribution in NSW. There are scattered records from the New England Tablelands and North West Slopes (OEH 2012).

Roosts in caves (near their entrances), crevices in cliffs, old mine workings and i n the disused, bottle-shaped mud nests of the Fairy Martin (Petrochelidon ariel) (OEH 2012). Large-eared Pied Bats frequent low to mid-elevation dry open forest and woodland, and well-timbered areas containing gullies close to roosts. The relatively short, broad wing combined with the low weight per unit area of wing indicates manoeuvrable flight. This species probably forages for small, flying insects below the forest canopy.

A variety of foraging habitats are used by the Southern Myotis, this species although it is usually found near large bodies of water, including estuaries, lakes, reservoirs, rivers and l arge streams, often in close proximity to their roost site. The species apparently has specific roost requirements,

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and only a s mall percentage of available caves, mines, tunnels and c ulverts are used by this species.

The Southern Myotis is considered comparatively rare over its limited national range (Richards 1995). The species is considered rare and sparsely distributed in a variety of habitats associated with water in Victoria (Lumsden & Menkhorst 1995). G enerally small colony sizes, relatively low reproductive rates (one to two young per year), and the specific roost requirements suggest that local populations are susceptible to impacts from even minor modifications or disturbances to roosting and foraging habitats.

Loss of roost sites and f oraging habitats are considered the major threats to this species. T he specific nature of its foraging habits suggest that this species is adversely impacted by habitat degradation through water pollution, and foraging habitat is likely to have been lost through nutrient enrichment, oil spills and pollutant rich run-off entering waterways. Disturbance of colonies, especially during the colder months when the bat is hibernating, may cause populations to desert roost sites, and can result in heavy mortality. The degradation of waterways through sedimentation, eutrophication, acidification and pollution may have altered the aquatic biota of foraging habitats or affected the abundance of prey populations. Widespread clearing of riparian forests may have affected the diversity of insect prey in these areas, which in turn may affect the densities of Myotis populations in these areas. T he modification of hydrological regimes may also affect the prey resources of this species.

Recorded roost sites include caves, mines, tunnels, culverts, spaces and scuppers under bridges and in buildings, Fairy Martin nests, in dense foliage in tropical areas, and f rom tree hollows in Victoria (Lumsden & Menkhorst 1995). The Southern Myotis has been reported feeding on flying insects (including beetles, flies, moths and grasshoppers), aquatic insects (such as boatmen) and small fish (such as the introduced Mosquito Fish.


The study area provides known and potential foraging habitat for the assessed species. These species are predominantly cave-roosting bats, although they may roost in artificial structures such as bridges and c ulverts. There is potential for a r oosting site to occur in existing culverts under the highway, however these would not be impacted by the proposal. No caves or abandoned mine shafts have been recorded in the proposal boundary and the proposal is not expected to impact on the maternity life-cycle activities of these species. The location of any roost sites for these species in the regional area is not known. No roosting bats were found under the Dignams Creek bridge and the bridge would not be removed as part of this proposal.

The loss of 20 hectares of forest habitat may impact on the potential breeding habitat for prey species (invertebrates) and therefore potentially lead to reduction of populations associated with increased pressure on a local scale. However comparable habitats are well represented throughout the locality and region. Therefore foraging habitat and prey abundance may be impacted by the

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proposal however the overall magnitude of this impact is very small relative to the extent of insect breeding resources in the study area


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No areas of habitat would become isolated. Microbat species are readily able to fly across fragmented habitats including major roads, however there is some evidence from research on microbats in Europe suggesting that microbats avoid highways (Berthinussen & Altringham 2012), are road casualties (Lesinski et al. 2010) and favour particular crossing sites on highways (Abbott et al. 2012) such as bridge underpasses. Therefore the proposal would potentially create a barrier to these species; however underpass structures including large culverts and the bridge over Dignams Creek will potentially facilitate microbat crossings.

Habitats adjacent to the road and within the proposal footprint provide potential resources for these species in terms of an area of habitat for insect prey species however it is unlikely that the proposal area contains an important roost site, such as a maternity or hibernation roost. There is potential for a roosting site to occur in existing culverts under the highway, however these would not be impacted by the proposal. There is a considerable amount of similar habitats for foraging in the surrounding landscape including conservation reserves and private lands.


Critical habitat has not been declared for these species.


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There is no recovery plan for these species. There are 15-25 priority action statements for each of species related to scientific research, community awareness and protection of these species. Considering the low potential impact to habitat for these species and the proposed avoidance and mitigation measures to minimise habitat removal including appropriate design of the infrastructure to avoid ecological impacts, the re-establishment of native vegetation and reuse of habitat attributes, the proposal is consistent with these priority actions.


Key threatening processes that are relevant to these species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be mitigated by the proposal. The main key threatening processes relevant to these species that are directly enacted by the proposal are those associated with clearance and degradation of foraging and roosting habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality and habitat degradation from feral herbivores. It is considered unlikely that the proposal would increase the likelihood of predation on this species by feral carnivores.

DIRECT IMPACT



Loss of hollow-bearing trees trees, and bushrock. Proposed avoidance and mitigation measures Bushrock removal include:

The proposed upgrade has been designed to minimise vegetation clearing where possible and minimise potential impacts to threatened species habitat.

A flora and fauna management plan would be developed as part of the Construction Environment Management Plan (CEMP) which provides specific details for the re-establishment of native vegetation

Removal of dead wood and dead on batters, cut faces, surrounding sediment basins and other areas trees disturbed during construction.

INDIRECT IMPACT



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The provision of vehicle and boot wash down facilities and ensure vehicles and f ootwear is free of soil before entering or exiting the site.
















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Conclusion

Considering the small area of foraging habitat that would be removed relative to the extent of similar habitats in the locality the proposal is unlikely to constitute a s ignificant impact to these three microbat species. There would be no impacts to potential artificial roost sites, with impacts limited to a relatively small area of foraging habitat and potential temporary roost sites in hollow trees. Considering the limited potential impacts described above an SIS is not considered to be required.

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Tree-roosting microbats (Eastern False Pipistrelle, Eastern Freetail-bat, Yellow-bellied Sheathtail-bat, Greater Broad-nosed Bat)

All four species are listed as vulnerable in NSW under the TSC Act. The Eastern False Pipistrelle, Eastern Freetail-bat and Greater Broad-nosed Bat were recorded in the study area during surveys for this project.

Habitat requirements of Eastern False Pipistrelle are poorly known although it has been reported from rainforest, wet and dry sclerophyll forests and woodland. T he species tends to be m ore common at higher altitudes than on the coast. Studies suggest that this species prefers wet habitats, especially riparian or high rainfall areas, where trees are greater than 20 metres in height (Menkhorst & Lumsden 1995), although a range of other habitats are used, including woodland.

Given the shape and size of its wings, the Eastern False Pipistrelle is likely to be a fast flying but not very manoeuvrable species, and probably forages above or just below the forest canopy, in open woodland or over water (Phillips 1995). This species has been reported feeding on moths, beetles, chafers, weevils, plant bugs, flies and ants (Australian Museum Business Services 1995 E astern False Pipistrelle roost predominantly in tree hollows, where groups of up to 10 individuals have been reported (Phillips & Inwards 1985). Individuals have also been reported utilising caves and abandoned buildings (Australian Museum Business Services 1995).

The Eastern Freetail-bat is found along the east coast from south Queensland to southern NSW. Occur in dry sclerophyll forest, woodland, swamp forests and m angrove forests east of the Great Dividing Range (OEH 2012). Roosts mainly in tree hollows but will also roost under bark or in man-made structures (OEH 2012). Usually solitary but also recorded roosting communally, probably insectivorous (OEH 2012).

The Greater Broad-nosed Bat is most common in the gullies and river systems draining the Great Dividing Range, from north-eastern Victoria to the Atherton Tableland in tropical Queensland, but it extends to the coast over much of its range (Hoye & Richards 1995). It is regarded as uncommon to rare, but may prove to be more widespread than currently indicated (Hoye & Richards 1995; Parnaby 1992). The main threat to this species is the loss of tree hollows, which are used as roost sites, through clearing or apiary. Habitat modification and clearing for agriculture may reduce foraging habitat and insect prey availability.

This species has been recorded in a variety of habitat types including rainforest, moist and dry eucalypt forest and woodland. Favoured foraging areas for this species appear to be t ree-lined creeks and the junction of woodland and cleared paddocks. Large emergent trees, including dead trees, with hollows are likely to be essential as roost sites. Greater Broad-nosed Bats feed on moths, beetles and other large slow-flying insects, and possibly other bats. A low, slow-flying species which utilises a large foraging area, the open nature of eucalypt woodland suits its direct flight pattern. Within denser vegetation types, use is made of natural and man-made openings such as roads, creeks and small rivers, where it hawks backwards and forwards for prey (Hoye & Richards 1995).

The Yellow-bellied Sheathtail-bat is dependent on suitable hollow-bearing trees to provide roost sites, which may be a limiting factor on populations in cleared or fragmented habitats. Flying insects (particularly beetles, grasshoppers, chafers and bugs) are taken above the forest canopy, and closer

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to the ground in low vegetation types (mallee, heath, mangroves). The fast direct flight pattern allows for prey to be encountered at a greater rate in cleared and open areas (Rhodes & Hall 1997).

This species is apparently usually solitary, but small colonies of up t o 10 individuals are not uncommon. In one case, a colony of 29 individuals was found within a hollow in the top of a dead eucalypt in predominantly cleared grazing land south-west of Brisbane. This clumping may have resulted from a lack of suitable roosting hollows in the locality or aggregations during winter by this species (Rhodes & Hall 1997).

Little is known of the nightly foraging movements or seasonal and regional movements of this species. Some regional migrations have been suspected, but no obs ervations have been documented which conclusively demonstrate this. Similarly, the breeding biology is poorly known, with births occurring from December to March.

Populations may have been reduced through clearing for agriculture and development, which has removed roost trees and foraging areas. This loss of habitat is likely to be the most significant threat to this species, but predation by cats may also constitute a localised threat to some colonies. The Yellow-bellied Sheathtail-bat may have always occurred at low numbers (populations may have been limited by the low availability of high-flying late emerging insect prey or by interspecific and intraspecific competition). The species may be more common than records indicate as flight habits and late emergence from roosts may make observation of this species difficult during general fauna surveys.


The proposal would result in the removal of potential foraging habitat comprising 20 hectares of forest habitats. There would also be the removal of up to 20 hollow trees potentially used as roosting habitat and maternity sites by these species. However potential habitats in the locality are extensive and include conservation reserves, state forests and private lands.

Considering the small proportion of habitat being impacted in the proposal area relative to the available habitat in the locality, viable local populations of these species are unlikely to be placed at risk of extinction. Continued use of surrounding retained habitats could be expected by these wide-ranging species considering the majority of these species have been recorded adjacent to the existing Princes Highway in the study area.


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The proposal would result in the removal of potential foraging habitat comprising 20 hectares of forest habitats. There would also be the removal of up to 20 hollow trees potentially used as roosting habitat and maternity sites by these species. However potential habitats in the locality are extensive and include conservation reserves, state forests and private lands. The proposal includes the provision of nest boxes to replace hollows lost in addition to pre-clearance surveys.

Considering the small proportion of habitat being impacted in the proposal area relative to the available habitat in the locality, viable local populations of these species are unlikely to be placed at risk of extinction. Continued use of the road corridor could be expected by these wide-ranging species.

No areas of habitat would become isolated. Microbat species are readily able to fly across fragmented habitats including major roads, however there is some evidence from research on microbats in Europe suggesting that microbats avoid highways (Berthinussen & Altringham 2012), are road casualties (Lesinski et al. 2010) and favour particular crossing sites on highways (Abbott et al. 2012) such as bridge underpasses. Therefore the proposal would potentially create a barrier to these species, however underpass structures including large culverts and the bridge over Dignams Creek will potentially facilitate microbat crossings.

Habitats in the proposal footprint potentially have some importance for the local population for foraging and potentially for shelter, however relative to the extent of habitat in the locality the impact represents a small proportion of the available habitat for the local population.


Critical habitat has not been declared for these species.


There is no recovery plan for these species. There are 16-21 priority action statements for each of species related to scientific research, community awareness and protection of these species. Considering the low potential impact to habitat for these species and the proposed avoidance and mitigation measures to minimise habitat removal including appropriate design of the infrastructure to

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minimise ecological impacts, such as minimising the size of fill batters where appropriate, avoiding hollow tree removal where possible during construction, the re-establishment of native vegetation and provision of nest boxes and r e-use of hollows, the proposal is consistent with these priority actions.


Key threatening processes that are relevant to these species are listed below, including reference to direct impacts and potential indirect impacts from key threatening processes and how each of these would be mitigated by the proposal. The main key threatening processes relevant to these species that are directly enacted by the proposal are those associated with clearance and degradation of foraging and roosting habitat. Potential indirect impacts include the introduction or spread of pathogens and weeds which may alter habitat quality, increased competition with feral honey bees for hollow resources and habitat degradation from feral herbivores. It is considered unlikely that the proposal would increase the likelihood of predation on this species by feral carnivores.


DIRECT IMPACT


Loss of hollow-bearing trees trees, and bushrock. Proposed avoidance and mitigation measures Bushrock removal include:

The proposed upgrade has been designed to minimise vegetation clearing where possible and minimise potential impacts to threatened species habitat.

A flora and fauna management plan would be developed as part of the Construction Environment Management Plan (CEMP) which provides specific details for the re-establishment of native vegetation

Removal of dead wood and dead on batters, cut faces, surrounding sediment basins and other areas trees disturbed during construction.

A nest box management strategy would be developed as part of the CEMP. The number and type of nest boxes required would be determined during the pre-clearance surveys based on the number, quality and size of the hollows that would be removed. The nest box management plan would detail the specifications for nest box dimensions, target species, installation requirements, locations of nest boxes and ongoing monitoring and maintenance.

Woody debris and bushrock would be re-used on site for habitat improvement where applicable and would be detailed in the landscape management plan/CEMP. Suitable areas for re-use may include the approaches to fauna underpasses, beneath the proposed bridge structure at Dignams Creek and rehabilitation

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areas.

















INDIRECT IMPACT







While the proposal would not directly increase bee numbers, the removal of hollow-bearing trees would indirectly increase competition for hollows by native fauna because the loss of tree hollows via occupation by feral honeybees reduces the number of hollows available for native animals to

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breed and shelter.





Conclusion

A number of mitigation measures have been recommended and would be implemented as part of an overall construction environmental management plan (CEMP). Avoidance and mitigation measures being implemented to reduce the impact to habitats for tree-roosting microbats comprise:

Appropriate road design to avoid ecological impacts where possible.

As part of the CEMP opportunities to avoid areas of foraging habitat and hollow trees during construction will be i nvestigated and t he proposed clearing boundary adjacent to the habitats/hollow trees to be retained will be delineated on the ground to avoid accidental incursions into adjacent areas.


A landscape management plan would be developed as part of the CEMP which provides specific details for the re-establishment of native vegetation on batters, cut faces, surrounding sediment basins and other areas disturbed during construction.

A nest box management strategy would be developed as part of the CEMP. The number and type of nest boxes required would be determined during the pre-clearance surveys based on the number, quality and size of the hollows that would be removed. Nest-boxes designed for tree-roosting microbats will be included in the strategy. The nest box strategy would require the installation of 70 per cent of nest boxes at least 3-6 months prior to the removal of any vegetation

Develop planning and procedures for a staged habitat removal process to consider the safe and ethical handling of fauna as outlined in the RMS Biodiversity Guidelines (RTA 2011).

Considering the above avoidance and mitigation measures, small area of habitat that would be removed relative to the extent of similar habitats in the locality the proposal is unlikely to constitute a significant impact to these four microbat species.

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F.2 Environment Protection and Biodiversity Conservation Act 1999 Vulnerable Flora – Square Raspwort (Haloragis exaltata subsp. exaltata)

Lead to a long-term decrease in the size of an important population An ‘important population’ is a population that is necessary for a species’ long-term survival and recovery. This may include populations identified as such in recovery plans, and/or that are:

key source populations either for breeding or dispersal populations that are necessary for maintaining genetic diversity, and/or populations that are near the limit of the species range.

Square Raspwort (Haloragis exaltata subsp. exaltata) was identified in relatively high abundance along the edges of Dignams Creek within and surrounding the study area and is likely to be part of an important population as defined under the EPBC Act. Square Raspwort has been found patchily along Dignams Creek from about 1.2 kilometres north-west of the bridge to where the creek enters Wallaga Lake, it is abundant on Snake Island in the Dignams Creek delta, and is scattered around the shoreline of Wallaga Lake, including the lower end of its other major tributary, Narira Creek (Miles and Cameron 2007).

Searches for Square Raspwort along Dignams Creek are summarized in Table E-1, comprising data collected during the current study as well as previous surveys. As can be seen from the results displayed in Table E-1 the abundance of this species is very variable and has increased since the original surveys. It is invariably found at sites where disturbance such as flooding, physical disturbance, or fire has exposed bare soil and created canopy gaps (Miles and Cameron 2007).

Table F-2: Results of surveys undertaken for Square Raspwort

Survey Results

Miles and Cameron (2007) undertook a survey of the non-tidal areas of Dignams Creek during 2006.

Several hundred plants were identified scattered along 3 kilometre of creek frontage. An additional 3 k ilometre searched immediately upstream had no plants.

NGH Environmental under took targeted surveys during 2008

Found to fairly common along banks of Dignams Creek. Not identified along any tributaries of Dignams Creek. Approximately 75 plants were identified in the study area.

Targeted surveys undertaken by SKM during 2011.

Up to 900 plant clumps recorded along Dignams Creek approximately 150 metres to the north and 250 metres to the south of the Princes Highway. Dignams Creek was flooded prior to the surveys being undertaken with many plants partly buried beneath soil, fallen trees and other debris, and this disturbance event is likely to encourage further germination of the species. Of the approximate 900 plant clumps recorded in the wider area, approximately 40 would be potentially impacted by the proposal. The distribution of Square Raspwort appeared to extend upstream and downstream of the area surveyed.

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Only a small proportion of the local population of Square Raspwort would be impacted from the proposal and it is highly likely that there would be significant regeneration of this species in areas disturbed during construction. The potential impacts would comprise removal of approximately 4.4 per cent of the population recorded along Dignams Creek 150 metres to the north and 250 metres to the south of the Princes Highway, and this proportion would be considerably less when considering the broader population in the local area. Prior to construction, Square Raspwort individuals to be retained would be protected (i.e. flagged and identified to construction staff) where possible.

Considering the small proportion of plants removed relatively to the larger population in the local area and the high colonising and regenerative capacity of this species the proposal is considered unlikely to result in a long-term decrease to the population.

Reduce the area of occupancy of an important population

Vegetation clearing in riparian areas would be minimised where possible to avoid erosion of creek banks and therefore some areas of potential habitat would remain intact potentially including Square Raspwort individuals. Connectivity for the transfer of genetic material of this species would be maintained under the bridge structure and it is likely that Square Raspwort would colonise any disturbed areas following construction where sufficient light and moisture is available.

Considering the very small area of habitat for Square Raspwort proposed to be impacted (0.15 hectares), the larger areas of high quality habitats upstream and downstream of the proposal, the temporary nature of the impacts and the implementation of avoidance measures the proposed road upgrades are considered unlikely to significantly reduce the area of occupancy Square Raspwort.

Fragment an existing important population into two or more populations The population would temporarily be fragmented from clearing impacts during construction, however vegetation clearing in riparian areas would be minimised where possible to avoid erosion of creek banks and therefore some areas of potential habitat would remain intact potentially including Square Raspwort individuals. Connectivity for the transfer of genetic material of this species would be maintained under the bridge structure and it is likely that Square Raspwort would colonise any disturbed areas following construction where sufficient light and moisture is available.

Adversely affect habitat critical to the survival of the species

Habitat critical to the survival of a species refers to areas that are necessary for activities such as:

Foraging, breeding, roosting, or dispersal.

For the long-term maintenance of the species including the maintenance of other species essential to the survival of the species, such as pollinators.

To maintain genetic diversity and long-term evolutionary development.

For the reintroduction of populations or recovery of the species.

A small area of habitat (0.15 hectares) would be t emporarily disturbed during construction of the proposed bridge structure over Dignams Creek. Vegetation clearing in riparian areas would be minimised where possible to avoid erosion of creek banks and t herefore some areas of potential

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habitat would remain intact potentially including Square Raspwort individuals. It is likely that Square Raspwort would recolonise disturbed areas following construction where sufficient light and moisture is available. Therefore it is unlikely that habitat would be adversely affected in the long term. This small area of habitat is unlikely to be critical to the survival of the species considering the relatively large area of potential habitat upstream and downstream of the proposal.

Disrupt the breeding cycle of an important population

The dispersal and germination of Square Raspwort appears associated with disturbance events including flooding, physical disturbance and fire (Miles and Cameron 2010). High levels of germination have been observed on areas of exposed bare earth with higher levels of light at ground level than would be present when the local vegetation community is intact (Miles and Cameron 2010). Considering this, it is unlikely that the proposal would alter the germination and dispersal of Square Raspwort, and riparian areas disturbed during construction are likely to be recolonised by Square Raspwort where sufficient light and moisture is available.

Modify, destroy, remove, or isolate or decrease the availability or quality of habitat to the extent that the species is likely to decline

The proposal would result in the removal of approximately 50 individuals from the local population. The population would temporarily be fragmented from clearing impacts during construction, however vegetation clearing in riparian areas would be minimised where possible to avoid erosion of creek banks and therefore some areas of potential habitat would remain intact potentially including Square Raspwort individuals. Connectivity for the transfer of genetic material of this species would be maintained under the bridge structure and it is likely that Square Raspwort would colonise any disturbed areas following construction where sufficient light and moisture is available.

Considering the small proportion of plants removed relatively to the larger population in the local area and the high colonising and regenerative capacity of this species the proposal is considered unlikely to modify, destroy, remove, isolate or decrease the availability or quality of habitat to the extent that the species is likely to decline.

Result in invasive species that are harmful to a vulnerable species becoming established in the vulnerable species habitat

The study area currently supports a diversity of weed species including noxious species (refer to Table 3-3). Specific weed management measures would be i mplemented to limit the spread of environmental weeds into areas of remnant vegetation.

A weed management plan would be developed as part of t he CEMP, the RMS Biodiversity Guidelines (RTA 2011) and the Introductory Weed Management Manual (Natural Heritage Trust 2004) provide guidance for developing weed management plans. As part of the weed management plan a s ite assessment by an ec ologist or person trained in weed identification and m anagement would be required to assess the extent and severity of weed species in the construction footprint with particular emphasis on noxious weed species.

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The weed management plan would include descriptions and m apping of major weed infestations during pre-clearing surveys and appropriate management actions to be undertaken for each infestation. The details of the weed management plan would vary for each site but would include:











Introduce disease that may cause the species to decline

There has been no disease pathogens recorded at the site to date, although testing and survey for the presence of pathogens is likely to be limited. If there is potential for equipment, machinery and personnel to spread disease affecting flora species including Phytophthora cinnamomi then the RMS have developed appropriate protocols to be implemented during construction. These are outlined in the Biodiversity Guidelines (RTA 2011).

Interferes substantially with the recovery of the species

The proposal would not conflict with the recovery of this species as only a small proportion of the available habitat for Square Raspwort would be temporarily impacted, and it is likely that Square Raspwort would recolonise areas disturbed during construction.

Conclusion

Considering the small proportion of plants removed relatively to the larger population in the local area and the high colonising and regenerative capacity of this species the proposal is considered unlikely to have a significant impact on S quare Raspwort, However an EBPC Act referral will be made to the Federal Minister of DSEWPaC to determine if the proposal is a controlled action.

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Endangered fauna Spotted-tailed Quoll

Lead to a long-term decrease in the size of a population

Spotted-tailed Quolls are known and predicted to occur in the locality and the range of habitats including large patches of native vegetation as well as farmland render the area suitable for this species. Potential impacts for the species are associated with the loss of habitat including potential den sites, habitat for prey species, fragmentation and the barrier effect of the highway potentially leading to increased genetic isolation and d ecreased dispersal ability. The species is known to frequent roadsides feeding on roadkill, thereby placing them at risk of vehicle strike. The severity of the impact in the locality is likely to be m inor considering the large home-range of the species occurring at low densities and wide ranging dispersal abilities. The potential barrier effect and fragmentation impacts would be a dequately mitigated with the installation of the targeted fauna connectivity measures for this species (e.g. underpasses and bridge).

The species typically has a large home range and occupies a diversity of habitat types. It is therefore difficult to identify the area of occupancy. Theoretically, quolls could occur in any of the larger forest fragments of the study area. Preferred habitat includes dry and moist sclerophyll forests and may include adjacent modified patches of forest on farmland. Suitable habitat is well represented in the larger fragments of forest in the region associated with several state forests and conservation reserves. The potential impact to habitat for prey species and life-cycle activities associated with the proposal represents a very small proportion of available habitat approximately in this locality.

Other life-cycle attributes include movements and dispersal. To mitigate this, the proposed upgrade would provide four underpass structures and a bridge targeting a range of fauna species including the quoll.

As such, breeding, foraging and movement life-cycle opportunities would remain in the region and likely to sustain local populations such that there is unlikely to be a l ong-term decrease of local populations associated with this proposal. Large areas of suitable habitat remain in the locality in rural holdings and cumulative development pressures in not currently expected.

Reduce the area of occupancy of a population

The species typically has a large home range and occupies a diversity of habitat types. It is therefore difficult to identify the area of occupancy. Theoretically, Quolls could occur in any of the larger forest fragments of the broader locality and suitable habitat is very widespread. No Spotted-tail Quoll were recorded during the surveys for this project, however records are present on pr ivate property approximately 200 metres to the north of the construction footprint. Preferred habitat includes dry and moist sclerophyll forests and may include adjacent modified patches of forest on farmland. Suitable habitat is well represented in the larger fragments of forest in the study area, particularly national parks, state forests and adjoining private properties. The proposal would remove potential habitat for the species however the overall reduction of habitat is a small proportion of the available potential habitat.

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Fragment an existing population into two or more populations

The existing highway in this location bisects large contiguous areas of habitat and t he proposed upgrade would also create a bar rier to movements of fauna. However the proposal would aim to mitigate this through the provision of targeted fauna underpasses including the proposed new bridge over Dignams Creek. The species has potential to cross the existing highway in the study area and any local populations are likely to extend to the east and w est of the highway given the large expanses of habitat available. It is unlikely that the proposal would fragment an existing population.







Some of the larger habitats represented in the study area are suitable for populations of spotted-tailed quoll and may constitute habitat critical to their survival. Suitable habitat is well represented in the larger fragments of forest in the study area, particularly national parks, state forests and adjoining private properties. The proposal would remove potential habitat for the species however the overall reduction of habitat is a small proportion of the available potential habitat.

Disrupt the breeding cycle of a population

Given the typically large home range of this species, potentially only a small number of individuals may be present in the lands surrounding the study area. There are no cave sites or suitably large logs present that may be considered to provide potential den sites for breeding. The proposal is therefore unlikely to impact on the breeding cycle of an important population.


Preferred habitat includes dry and moist sclerophyll forests and m ay include adjacent modified patches of forest on farmland. Suitable habitat is well represented in the larger fragments of forest in the region associated with several state forests and conservation reserves including Kooraban and Gulaga National Park. The potential impact to habitat for prey species and life-cycle activities associated with the proposal represents a very small proportion of available habitat approximately in this locality.

The small area of habitat to be removed is not considered unique for this species and is widespread throughout the sites and surrounding landscape. Continued use of the habitats could be reasonably expected. The activity would not cause the isolation or fragmentation of habitat.

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Result in an invasive species that are harmful to an endangered species becoming established in the endangered species habitat

The potential for weed invasion or dieback from plant pathogens is considered possible with a proposal of this nature and appropriate controls are required to reduce this threat as it may have long term implication for the habitat of the species. The management of these threats would be managed under the guidance of a Flora and Fauna Management Plan to be prepared as part of the CEMP.

Introduce disease that may cause the species to decline The potential for dieback from plant pathogens is considered possible with a proposal of this nature and appropriate controls are required to reduce this threat as it may have long term implication for the habitat of the species. The management of these threats would be managed under the guidance of a Flora and Fauna Management Plan to be prepared as part of the CEMP.

Interferes substantially with the recovery of the species The proposal would not conflict with the recovery of this species, as it would only have an effect on a very small proportion of potential habitat and would not impact on potential breeding habitat.

Conclusion Suitable habitat is well represented in the larger fragments of forest in the region associated with several state forests and conservation reserves. The potential impact to habitat for prey species and life-cycle activities associated with the proposal represents a very small proportion of available habitat approximately in this locality. Other life-cycle attributes include movements and dispersal. To mitigate this, the proposed upgrade would provide four underpass structures (two in Stage 1 and two in Stage 2) and a bridge (Stage 1) targeting a range of fauna species including the quoll.

As such, breeding, foraging and movement life-cycle opportunities would remain in the region and likely to sustain local populations such that there is unlikely to be a significant impact on this species.

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Vulnerable fauna Grey-headed flying-fox

Lead to a long-term decrease in the size of an important population

The Grey-headed flying-fox is a habitat specialist that occurs widely throughout the south coast region. T here were no camps or roost sites identified in the study area. This species was not identified foraging on the site during the field survey however the forested habitats are expected to provide potentially important foraging habitat for the Grey-headed Flying-fox. There is no evidence to suggest that there is an important population occurring with the proposed investigation area.

The Grey-headed flying-fox feeds on n ectar and pollen of a r ange of native trees, in particular species form the plant genera Eucalyptus, Melaleuca, Banksia and Ficus and fruits of rainforest trees and vines. There are extensive areas of potential foraging habitat for the species throughout the broader locality and the clearing of around 0.2 hectares of potentially important foraging habitat for this species represents a r elatively minor impact in the context of the foraging range of local populations. In relation to the available habitat in adjacent surrounding areas, the proposal is not considered likely to affect this species at the local level. The proposed action is unlikely to affect the feeding, breeding or gestation lifecycles of local Grey-headed Flying-fox populations.

The three important aspects considered in assessing the impacts on t his population from the proposal relate to relevant actions as listed in the draft National Recovery Plan for the Grey-headed Flying Fox (DECCW 2009) and whether the proposal is consistent with these actions. These considerations are;

Identify and protect foraging habitat critical to the survival of the Grey-headed Flying-fox across their range

To protect and i ncrease the extent of key winter and spring foraging habitat of Grey-headed Flying-foxes

To identify roosting habitat critical to the survival of Grey-headed Flying-foxes.

The proposal is considered consistent with these objectives, in that the proposed activity would not directly impact on an identified roost camp or winter flowering eucalypt species.


The proposed action would reduce the available foraging habitat for local populations by a very small percentage when considering the total known area of habitat available. The proposal is not expected to significantly impact on food resources available for local populations of the grey-headed flying-fox. This species is wide ranging a capable of exploiting seasonally available and wide spread food resources.

Fragment an existing population into two or more populations

The proposal would involve temporary disturbance to vegetation and would not contribute to the cumulative fragmentation of habitat in the landscape. Highly mobile species such as bats and birds

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are expected to be less impacted by fragmentation and the grey-headed flying-fox is particularly well adapted to accessing widely spaced habitat resources given its mobility and preference for seasonal fruits and blossom. The proposal would not fragment an important population of the Grey-headed flying-fox.







Forests that contain spotted gum are considered critical foraging habitat for the Grey-headed Flying-fox (DECCW 2009) due to their flowering period which coincides with the final weeks of gestation, and during the weeks of birth, lactation and conception of the grey-headed flying-fox (Sept-May). The proposal would not impact on spotted gum forest, and would not impact on a roost camp site.


No evidence of a roosting colony of the grey-headed flying-fox occurs on the study site. The nearest known colony is approximately 12 kilometres to the southeast near Bermagui.


As stated, the proposal would remove up to 20 hectares of forest habitat. The proposed action would decrease the available foraging habitat for local populations by a very small percentage when considering the total known area of habitat available throughout conservation reserves, state forests and private lands. The proposal is not expected to isolate access to the remaining habitat on site for this wide-ranging and highly mobile species.

It is unlikely that this proposal would directly lead to the decline of the species in the broader locality.


The potential for dieback from plant pathogens is considered possible with a proposal of this nature and appropriate controls are required to reduce this threat as it may have long term implication for the habitat of the species. The management of these threats would be managed under the guidance of a Flora and Fauna Management Plan to be prepared as part of the CEMP.


There are no known disease issues affecting this species. The proposal is unlikely to increase feral animal abundance or the potential for significant disease vectors to affect local populations. There is

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potential for equipment, machinery and personnel to spread disease including Phytophthora cinnamomi affecting fauna species including habitat for this species. An appropriate procedure would be used to reduce this risk including the washing and disinfecting of equipment and other plan containing mud or soil between sites.


The proposal would not conflict with the recovery of this species. The proposal investigation areas have been selected on the basis of avoiding as much habitat as possible.

Conclusion The proposed action would reduce the available foraging habitat for local populations by a very small percentage when considering the total area of habitat available in the locality. The proposal is not expected to significantly impact on f ood resources available for local populations of the grey-headed flying-fox. This species is wide ranging a capable of exploiting seasonally available and wide spread food resources.

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Large-eared Pied Bat

Lead to a long-term decrease in the size of an important population The Large-eared pied Bat roosts in caves (near their entrances), crevices in cliffs, old mine workings and in the disused, bottle-shaped mud nests of the Fairy Martin (Petrochelidon ariel) (OEH 2012). Large-eared Pied Bats frequent low to mid-elevation dry open forests and woodland, and well-timbered areas containing gullies close to roosts. Given the absence of a r oost site within the proposal corridor there is no evidence of an i mportant population. Any use of the site would be considered for foraging activities only and the site habitat

Loss of roost sites and foraging habitats are considered the major threats to this species. The loss of 20 hectares of forest habitat may impact on the potential breeding habitat for prey species (invertebrates) and therefore potentially lead to reduction of populations associated with increased pressure on a local scale. However comparable habitats are well represented throughout the locality and region. Therefore foraging habitat and prey abundance may be impacted by the proposal however the overall magnitude of this impact is very small relative to the extent of insect breeding resources in the study area

Reduce the area of occupancy of an important population The proposal would remove about 20 hectares of vegetation comprising dry and wet open forest habitats potentially used by this species for foraging. This is a small percentage of the foraging habitat available throughout the distributional range of the species and there is currently no evidence to indicate that an important population is resident in the locality. The proposal is not expected to significantly impact on f ood resources available for local populations and would not impact on potential roosting habitat.

Fragment an existing important population into two or more populations

Highly mobile species such as bats are expected to be less impacted by fragmentation, particularly as existing vegetation would remain on-site. The proposal would not fragment an i mportant population of the Large-eared Pied Bat.

Adversely affect habitat critical to the survival of the species Habitat critical to the survival of a species refers to areas that are necessary for activities such as:





The proposed area of disturbance represents a very small fraction of the potential foraging habitat for the large-eared pied bat. As the species is a cave-roosting bat and there are no c aves in the study area, there would be no impact on potential roosting habitat.


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No evidence of a roosting colony of the large-eared pied bat occurs in proximity to the study area and the proposal would not impact on breeding cycles or potential breeding habitat.


The proposal would remove about 20 hectares of vegetation potentially used by this species for foraging. There would be a decrease in the availability of habitat in the region however this decrease represents a very small fraction of the potential foraging habitat for the species. No potential roosting habitat would be impacted as the species roosts in caves, which are not present on the site.



Introduce disease that may cause the species to decline The potential for dieback from plant pathogens is considered possible with a proposal of this nature and appropriate controls are required to reduce this threat as it may have long term implication for the habitat of the species. The management of these threats would be managed under the guidance of a Flora and Fauna Management Plan to be prepared as part of the CEMP.


The proposal would not conflict with the recovery of this species. The proposal footprint has been selected on the basis of avoiding as much habitat as possible and preserving habitat on site. The proposed activity does not conflict with the objectives of the national recovery plan for this species,

Conclusion The proposal would remove about 20 hectares of vegetation potentially used by this species for foraging. There would be a decrease in the availability of habitat in the region however this decrease represents a very small fraction of the potential foraging habitat for the species. No potential roosting habitat would be impacted as the species roosts in caves, which are not present on the site. The proposal is considered unlikely to impose a significant impact.

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Koala


There was no evidence of Koala reported in the study area and adjacent habitats from the targeted surveys. However there are known populations in contiguous forest areas to the south of Bermagui in several State Forests and National Park areas (DECC 2009) and the species was recorded at five sites in Kooraban National Park from surveys conducted by NPWS in 2005 ( reported in DECC 2009).

In a recent Koala surveys conducted by Allen (2011) in Kooraban and Gulaga National Park only 8% of the grid-sites assessed had e vidence of Koalas in the Kooraban/Gulaga area. Compared with most areas where this kind of survey is undertaken in the southern forests (Allen et al 2010), this activity rate is very low. These results suggest probably only 5-15 Koalas are surviving in the approximately 6,000 hectares of forests assessed. No Koala activity was reported close to the study area.

The two areas in the Kooraban National Park (the Sam’s Ridge and Jimmy’s Creek areas) where Koalas are persisting are those where Koalas had been i dentified previously both in anecdotal reports and i n previous surveys. T he continued persistence in these areas over at least several decades indicates some stability with these two breeding associations (Allen 2011). Both sites are located several kilometres to the west and northwest of the study area and there was no evidence of Koala activity within the study area.

By the 1960’s Koalas were known to be persisting to the east of the Princes Highway and south of Dignams Creek in what was to become the Wallaga Lake, and then in 2000, was incorporated in the Gulaga National Park. The species was also known from Dignams Hill, immediately to the west of this area which is incised by the Princes Highway. The evidence reported by Allen (2011) and in recent surveys of the regional area indicates that two small populations occur about 1.5 kilometres to the west of the proposal study area. These populations would be c onsidered important populations in the context of the interim referral advice provided by DSEWPaC (2012).

No Koala scats were recorded from the survey of 600 t rees on both sides of the highway (500 m wide) within the length of the study area (refer Appendix H). Any Koala activity in the study area is considered to be v ery low and the survey results suggest that the habitats adjoining the proposal corridor may only be used occasionally by dispersing individuals rather than supporting a portion of the local population or the home range of an individual.

Apart from the loss of habitat, Koalas may be i mpacted by alteration to movements and v ehicle strike. Currently connectivity for the Koala is restricted by the existing highway and there are no suitable underpasses. The proposed upgrade would aim to facilitate the natural movements of Koalas across the proposal corridor with suitable underpasses including a l arge bridge structure, underpass and fauna fencing.

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The proposal would remove a relatively small area of habitat (19.9 ha) containing known Koala feed tress but not known to be currently occupied by local populations or forming the home range of an individual. This clearing of habitat is considered minimal in relation to the extent of similar habitats containing feed tree species throughout Kooraban and Gulaga National Park and surrounds (c. 6000 ha) and t he evidence indicates that the study area may constitute a p otential east-west dispersal corridor for Koalas to access potential habitats in these reserves. These factors in addition to the proposed inclusion of targeted underpass structures for stage 1 and stage 2 to greatly improve the current poor connectivity between these two reserves suggest that the proposal is unlikely to lead to a long-term decrease in the size of an important population.


The DECC (2009) report for the Bermagui-Mumbulla area to the south of the study area indicates that the tree species under which Koala faecal pellets were most commonly found were Eucalyptus longifolia (woollybutt), E. globoidea (white stringybark), and E. muelleriana (yellow stringybark). While E. cypellocarpa (monkey gum), E. bosistoana (coastal grey box), E. tricarpa (red ironbark) and E. sieberi (silvertop ash) were less frequently encountered, but a relatively high proportion of these species also had Koala pellets underneath them. E. cypellocarpa (monkey gum) is also listed in the NSW Koala Recovery Plan (DECC 2008) as a s econdary food tree species for the south coast region.

The Australian Koala Foundation (AKF) also identifies additional tree species as primary or secondary species. In the Bega Valley and Eurobodalla LGA the AKF (2012) identifies monkey gum as a primary feed tree species and the majority of the species listed above have been identified as secondary species (refer to Table 3-6). In addition, Eucalyptus botryoides (bangalay) was also identified in the report as a secondary feed tree.

White stringybark, monkey gum and silvertop ash are all components of the vegetation map units 1 and 2 and 3 identified in the study area, and on this basis these habitats are considered potential Koala habitat and the proposal would remove around 19.9 hectares of potential Koala habitat. However the surveys for this species were designed to identify the activity levels of Koalas and these data were based from a s earch of over 600 t rees up t o 500 metres from the proposal. No evidence of any Koala activity was noted and the site habitats are considered to be more commonly used by dispersing individuals suggesting transient use. In this regard the proposal would not reduce the area of occupancy of the population but rather impact on an area of potential habitat as a link to other areas of potential habitat. .


The evidence gathered from a back ground review, and targeted surveys reported in Allen (2011) and this investigation suggest that two small populations occur in the wider locality and that these currently occur several kilometres to the west of the existing highway. However there is historical evidence of Koalas occurring in Gulaga to the east of the highway and continuing through to the coast as early as 40 years ago (Allen 2011). The upgrade of the highway in this location would not

294


fragment known important populations and would aim to facilitate the natural movements of Koalas across the proposal corridor between the two reserves in the future upon completion of stage 2.


According to the DSEWPaC Interim Koala Referral Advice for Proponents (2012), “habitat critical to the survival of the Koala is currently considered to be areas of forest or woodland where:

primary Koala food tree species comprise at least 30% of the overstorey trees, or primary Koala food tree species comprise less than 30% of the overstorey trees, but together

with secondary food tree species comprise at least 50% of the overstorey trees or, primary food tree species are absent but secondary food tree species alone comprise at least

50% of the overstorey trees, or the above qualities may be absent in a forest or woodland but other essential habitat features

are present and adjacent to areas exhibiting the above qualities, or a relatively high density of Koalas is supported, regardless of the presence of food tree species.

Koala population densities vary across their range and regional data should be used to judge relative density”.

These criteria have been applied to the field data to identify the proportion of Koala habitat for Koalas situated within the study area. The data used in this assessment includes detailed descriptions gathered for the vegetation community types and floristic composition and the proposal vegetation community mapping and other broad-scale mapping of the region as reported in Tozer et al (2010)

In addition to this recent research in the south coast region (DECCW 2010c) has established that eucalypt communities in which Eucalyptus longifolia (woollybutt), E. globoidea (white stringybark), and E. muelleriana (yellow stringybark), E. cypellocarpa (monkey gum), E. bosistoana (coastal grey box), E. tricarpa (red ironbark) and E. sieberi (silvertop ash) occur sustains the known Koala populations in this part of the region.

These feed trees are locally important and associated with frequent Koala activity (DECCW, 2010c), and are also recognised in the south coast area as secondary and supplementary Koala food trees (with the exception of E. tricarpa and E. sieberi) (DECC, 2008). There are no r ecognised primary feed tree species from the south coast region (DECC, 20080 recorded in the study area and only one secondary feed tree species, Monkey Gum (Eucalyptus cypellocarpa). The feed tree species identified in this biodiversity assessment occur within Map Units 1, 2, 3 in the study area (refer Table below).

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MU Vegetation types identified in the study area

Food tree species south coast region (DECC 2008) (% cover)

Important food trees south coast region (DECCW 2010c) additional to DECC (2008)

Primary food trees Bega Valley and Eurobodalla LGA (AKF 2012) additional to DECC (2008) and DECCW (2010c)

Habitat critical to Koala survival based on DSEWPaC (2012)

Habitat category, Callaghan unpublished in DECC (2008) Primary Secondary Supplementary Primary Other

1 Silvertop Ash – Stringybark dry open forest

None Monkey Gum (E.cypellocarpa) (<5%),

Yertchuk (E.consideniana) (<5%),

Coast Grey Box (E. bosistoana) (<5%)

Blue-leaved Stringybark (E.agglomerata) (>30%),

White Stringybark (E.globoidea) (10%),

Yellow Stringybark (E.muelleriana) (5%),

Silvertop Ash (E.seiberi) (>30%),

Red Ironbark (E.tricarpa) (<5%),



Monkey Gum (E.cypellocarpa) (<5%)

No Secondary habitat (class B)

2 White Stringybark dry open forest

None Monkey Gum (E.cypellocarpa) (10%),

Coast Grey Box (E. bosistoana) (<5%),

Woollybutt (E.longifolia) (<5%),

Blue Box (E.baueriana) (<5%)

Yellow Stringybark (E.muelleriana) (>30%),

White Stringybark (E.globoidea) (>30%),

Blue-leaved Stringybark (E.agglomerata) (5%)

Silvertop Ash (E.seiberi), (5%),

Rough-barked Apple (Angophora floribunda) (20%),




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3 Bangalay/ Blue Gum sheltered forest

None Monkey Gum (E.cypellocarpa) (<5%)

Yellow Stringybark (E.muelleriana) (>30%),

White Stringybark (E.globoidea) (10%)



Bangalay (E.botryoides) (>30%) occurs as a hybrid with Sydney Blue Gum (Eucalyptus saligna)


4 River Peppermint


Bangalay (E.botryoides)

No Tertiary habitat

– Rough- (10%) occurs barked as a hybrid Apple moist with Sydney shrubby forest

Blue Gum (Eucalyptus saligna)

5 Riparian forest


Bangalay (E.botryoides)

No Tertiary habitat

(5%) occurs as a hybrid with Sydney Blue Gum (Eucalyptus saligna)

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Based on the presence and proportion of eucalypt food tree species, none of the vegetation types fit the definition for habitat critical to the survival of Koalas, According to DECC (2008) Map unit 1 is secondary habitat (class B), map units 2 and 3 ar e secondary habitat (class C) and t he riparian habitat is classed as tertiary habitat.

However in relation to dot point 4 of the interim advice

the above qualities may be absent in a forest or woodland but other essential habitat features are present and adjacent to areas exhibiting the above qualities, or

The presence of two small Koala populations known from Kooraban National Park and surrounding contiguous areas and the presence of important food tree species reported from DECC (2010) suggests that essential habitat features are present and the study area may occur in an important corridor for dispersal of Koalas to currently unoccupied habitats east and west of the highway. Therefore as a precautionary measure the habitat is considered as critical to the survival of Koalas in the Dignams Creek area.

The proposal would impact on around 19.9 hectares of this habitat category which is a very small proportion of the habitat available to the species (at least 6000 hectares just across the two reserves). The greater impact could be associated with the potential interruptions to the potential dispersal of Koalas. At present the existing of the highway within the dispersal corridor would create a barrier to Koalas, and the proposed inclusion of targeted underpass structures aimed at facilitating the natural movements of koalas across the project corridor.


Given that the habitats within the proposal area have not been identified as a frequently used part of a home range territory for an i ndividual or the local population the proposal is not considered to disrupt the breeding cycle of the important populations identified in the region.

Modify, destroy, remove, or isolate or decrease the availability or quality of habitat tothe extent that the species is likely to decline

Recent Koala surveys conducted by Allen (2011) in Kooraban and Gulaga National Park suggest probably only 5-15 Koalas are surviving in the approximately 6,000 hectares of forests assessed across these two reserves. The proposal would remove around 19.9 hectares of habitat considered critical to the survival of Koalas. This is classed based on the presence of habitat containing potential food tree species and t he location of the habitat in the landscape which represents a potential dispersal corridor for Koalas. This is considered a minor loss of potential habitat in this locality given the presence of over 6,000 hectares of similar forests across these two reserves. Further the proposed inclusion of targeted crossing structures for Koalas aimed at facilitating the natural movements of koalas across the project corridor.

There would be a d ecrease in the availability of habitat in the region however this decrease represents a very small fraction of the potential habitat for the species and unlikely to lead to a decline in the local populations.

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The potential for weed invasion or dieback from plant pathogens is considered possible with a proposal of this nature and appropriate controls are required to reduce this threat as it may have long term implication for the habitat of the species. The management of these threats would be managed under the guidance of a Flora and Fauna Management Plan to be prepared as part of the CEMP. Suitable protocols have been developed under the RMS Biodiversity Guidelines (RMS 2011).



Koalas are vulnerable to Chlamydia and i nfertility and death can be ou tcomes. I n a s tudy of roadside Koala populations at Bonville several kilometres north of the proposal the prevalence of Chlamydia was high (AMBS 2011). Its incidence apparently doubled over two decades with a climb in the average from 15.2 incidents per year during the decade of 1991 to 2000 to 32.75 incidents per year during the decade of 2001 to 2010. It is unknown if this prevalence was related to the location of the population.

Chlamydia affects the fecundity of Koalas. While the disease seemed virulent in the Bonville study area, the rates of infection were similar to other areas in northern NSW and southern Queensland. The clearing of habitat for the proposal would not directly introduce the disease; however fragmentation of habitat has potential to isolate individuals. If Chlamydia is present in the local population, further fragmentation may have mixed effects, such as reduce the spread of the disease or may exacerbate the spread of the disease in roadside areas. The plan to provide targeted connectivity strategies for the Koala as part of the proposal is aimed at facilitating the natural movements of Koalas across the proposal corridor.

While Koala retrovirus is a known threat to the species, there is no account of this disease currently occurring in Kooraban National Park at present and the status of the diseases in the region is unknown. While disease may occur in local populations the proposal is unlikely to isolate or confound the problem particularly as targeted crossing structures are proposed to facilitate natural movements of Koalas.


The existing highway in this location is likely to provide a barrier to movements and the proposed new upgrade would improve this situation by placing targeted connectivity structures aimed at facilitating the natural movements of Koalas across the proposal corridor. This factor in addition to the proposed mitigation and monitoring activities would ensure that the proposal would be unlikely to

299


interfere substantially with the recovery of the species, providing mitigation measures to prevent population isolation are implemented.

Appropriate measures have been incorporated into the design of the road to minimise the impacts of fragmentation on t his species and i ts habitat and a llow continued access to potential habitat for foraging, breeding and dispersal. This includes purpose design underpass structures and K oala exclusion fencing (refer Section 5.2.5).

The Commonwealth Government has released the National Koala Conservation Strategy 2009-2014 which identifies the key threats to the species and outlines the actions required to stabilise the species.

The proposal would not conflict with the recovery of this species. The proposal footprint has been selected on the basis of avoiding as much habitat as possible and preserving habitat on site. The proposed activity does not conflict with the objectives of the national recovery plan for this species and aimed at facilitating the natural movements of Koalas across the proposal corridor.

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Long-nosed Potoroo


The potoroo inhabits coastal heaths and dr y and wet sclerophyll forests. Dense understorey with occasional open areas is an essential part of habitat, and may consist of grass-trees, sedges, ferns or heath, or of low shrubs of tea-trees or melaleucas. A sandy loam soil is also a common feature.

The species was not confirmed in the study area although is considered to have potential to occur. Conical diggings were noted in several locations however these are not distinguishable from the Long-nosed Bandicoot which was observed. The northern end of the proposal corridor, north of Dignams Creek provides suitable habitat for the species given that the soil type and dense understorey compared to the remainder of the study area. Based on known habitat preferences, habitats in the national park areas of the southern section would be c onsidered marginal for this species. There is unlikely to be an important population in the study area.



The northern end of the proposal corridor, north of Dignams Creek provides suitable habitat for the species given that the soil type and dense understorey compared to the remainder of the study area. Based on known habitat preferences, habitats in the national park areas of the southern section would be considered marginal for this species. There is unlikely to be an important population in the study area.


The proposal would not fragment an important population of the Long-nosed Potoroo. The design of a number of fauna connectivity structures would improve the current barrier effect of the existing highway in the study area.







301


The proposed area of disturbance represents a v ery small fraction of the potential habitat for the Long-nosed Potoroo.


No evidence of an important population of the Long-nosed Potoroo occurs in proximity to the study area. The proposal would remove potential habitat and t herefore potentially impact on breeding cycles or potential breeding habitat if a population does occur. The potential habitat present is only considered marginal for the species and a small fraction of the area of available habitat within the regional area.









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Giant Burrowing Frog


The species is found in heath, woodland and open dry sclerophyll forest on a variety of soil types except those that are clay based. The Giant burrowing frog spends more than 95% of its time in non-breeding habitat in areas up to 300 m from breeding sites. Whilst in non-breeding habitat it burrows below the soil surface or in the leaf litter. Individual frogs occupy a series of burrow sites, some of which are used repeatedly. The home ranges of both sexes appear to be non-overlapping suggesting exclusivity of non-breeding habitat. Home ranges are approximately 0.04 hectares in size. There is unlikely to be an important population in the study area.

Potential habitat was noted along Blinds Creek which is a tributary of Dignams Creek and also the upper reaches of Dignams Creek outside of the study area are also suitable. The lower portions of Dignams Creek impacted by the proposal appear to be too deep and rapid flowing to be suited as breeding sites for this species and are considered only very marginal. Breeding habitat of this species is generally soaks or pools within first or second order streams. They are also commonly recorded from 'hanging swamp' seepage lines and where small pools form from the collected water. As such the areas of potential breeding habitat noted are outside of the proposed proposal footprint and upstream of the activity outside of the zone of influence.

Some areas of non-breeding habitat near Blinds Creek may be impacted particularly on the south-side of Dignams Creek Road in loamy and sandy soils. The impact area would equate to less than 2-3 hectares.


Some areas of non-breeding habitat near Blinds Creek may be impacted particularly on the south-side of Dignams Creek Road in loamy and sandy soils. The impact area would equate to less than 2-3 hectares. There is unlikely to be an important population in the study area and the area is only considered as potential habitat.


The proposal would not fragment an important population of the Giant Burrowing Frog as this habitat is only considered marginal for the species. The design of a number of fauna connectivity structures would improve the current barrier effect of the existing highway in the study area.







303


The proposed area of disturbance fall outside the area identified as potential habitat for the Giant Burrowing Frog (i.e. Blind Creek catchment), and there would be no direct impacts on this habitat. Additional areas of potential habitat are expected upslope to the east of Dignams Creek.


Important breeding areas of habitat may occur within the region in the upper reaches of the Dignams and Blind Creek ecosystems, however not within the proposal area.


If present in the locality the preferred areas of habitat would occur in the upper reaches of Dignams Creek and Blind Creek upstream of the proposal corridor and outside of the zone of influence. The clearing for the proposal would not isolate areas of breeding or non-breeding habitat which would be retained outside of the construction zone.




The main pathogen affecting amphibian species comprises chytrid fungus which results in the disease chytridiomycosis. The exact transmission method of this species is largely unknown, however mitigation measures to limit the potential spread and exacerbation of the disease would be implemented. Mitigation measures to limit indirect impacts to aquatic habitats will limit the potential for the disease to be exacerbated in local frog populations.



The proposal would not conflict with the recovery of this species. The proposal footprint has been selected on the basis of avoiding as much habitat as possible and preserving habitat on site. The proposed activity does not conflict with the objectives of a national recovery plan for this species,

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Stuttering Frog


The species is found in rainforest and wet, tall open forest in the foothills and escarpment on the eastern side of the Great Dividing Range. Suitable habitat is widespread in the region particularly to the west of the study area in the more contiguous wet forests along the range and only considered marginal in the study area. There is unlikely to be an important population in the study area.






The clearing for the proposal would not isolate areas of breeding or non-breeding habitat which would be retained outside of the construction zone.







If present in the locality the preferred areas of habitat would occur in the upper reaches of Dignams Creek and Blind Creek upstream of the proposal corridor and outside of the zone of influence.


Important breeding areas of habitat may occur within the region in the upper reaches of the Dignams and Blind Creek ecosystems, however not within the proposal area.


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Migratory species

An area of ‘important habitat’ for a migratory species is:

• habitat used by a migratory species occasionally or periodically within a region that supports an ecologically significant proportion of the population of the species, and/or

• habitat that is of critical importance to the species at particular life-cycle stages, and/or

• habitat used by a migratory species which is at the limit of the species range, and/or

306


• habitat within an area where the species is declining.

Listed migratory species cover a broad range of species with different life cycles and p opulation sizes. Therefore, what is an ‘ecologically significant proportion’ of the population varies with the species. Some factors that would be considered include the species’ population status, genetic distinctiveness and species specific behavioural patterns (for example, site fidelity and dispersal rates). These factors have been considered in the following assessment.

Substantially modify (including by fragmenting, altering fire regimes, altering nutrient cycles or altering hydrological cycles), destroy or isolate an area of important habitat for a migratory species

There is no evidence to suggest that an ecologically significant proportion of the population of any identified migratory species exists within the proposal boundary.

Result in an invasive species that is harmful to the migratory species becoming established in an area of important habitat for the migratory species

The potential for weed invasion has been considered highly likely with a proposal of this nature and appropriate controls have been provided during the construction and operation of the road to reduce this threat as it may have long term implications for the habitat of threatened species. The management of invasive species would be managed under the construction environmental management plan.

Seriously disrupt the lifecycle (breeding, feeding, migration or resting behaviour) of an ecologically significant proportion of the population of a migratory species.

As discussed there is no evidence to suggest that an ec ologically significant proportion of the population of a migratory species exists within the proposal boundary.

REFERENCES

Allen, C., Saxon, M. and McDougall, K. (2010). Summary report on surveys conducted in 2007-2009 for Koalas in the coastal forests of the Bermagui/Mumbulla area. NSW Department of Environment, Climate Change and Water.

Allen, C. (2011). Koala survey Kooraban and Gulaga National Parks and adjacent lands 2010-2011. Unpublished report prepared by the NSW NPWS for volunteer and l ocal aboriginal land council participants.

Australian Museum Business Services. (1995). Fauna Impact Statement for the Gloucester and Chichester Management Areas. Report prepared for State Forests of NSW.

Debus, S. J. S. (1993). The Mainland Masked Owl Tyto novaehollandiae : a review in Aust. Bird Watcher, 15(4)., pp. 168 - 191.

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Debus, S. J. S. & Rose, A. B. (1994). The Masked Owl Tyto novaehollandiae in New South Wales in Aust. Birds 28 supplement., pp. 40 – 64

Debus, S. J. S. (1997). The Barking Owl in New South Wales. Australian Birds, 30(3), 53-80.

Department of Environment and C limate Change (DECC) (2008). Recovery Plan for the Koala (Phascolarctos cinereus). Department of Environment and Climate Change NSW. Sydney.

Department of Sustainability and Environment (DSE) (2005). Flying-fox Campsite Management Plan Yarra Bend Park.

Edgar, R. & Belcher, C. (1995). Spotted-tailed Quoll, pp. 67 - 69 in The Mammals of Australia. ed. R. Strahan, Australian Museum and Reed, Sydney.

Eby, P. (1996). Interactions between the Grey-headed Flying-fox Pteropus poliocephalus (Chiroptera: Pteropodidae) and its diet plants-seasonal movements and seed dispersal. Ph.D. Thesis. Armidale, NSW: University of New England.

Eby, P. (1998). An analysis of diet specialization in frugivore Pteropus poliocephalus in Australian subtropical rainforest. Australian Journal of Ecology. 23:443-456.

Eby, P. (2002). National Count of Grey-headed Flying foxes July 27 & 28, 2002. A report to Environment Australia, Canberra.

Eby, P. & D. Lunney (2002). Managing the Grey-headed Flying-fox as a threatened species in NSW. In: Proceedings of the Royal Zoological Society of New South Wales. Mosman, Sydney: Royal Zoological Society of New South Wales.

Goldingay, R. L. & Kavanagh, R. P. (1991). The Yellow-bellied Glider: a Review of its Ecology and Management Considerations. pp. 365 - 375 in Conservation of Australian Forest Fauna, ed. D. Lunney. Royal Zool. Soc. of NSW, Mosman

Goldingay, R. L. & Kavanagh, R. P. (1993). Home-range Estimates and Habitat of the Yellow-bellied Glider (Petaurus australis) at Waratah Creek, New South Wales. Wildl. Res. 20 : 387 - 404.

Goldingay, R.L. 1986. Feeding behcaviour of the yellow-bellied glider Petarus australis (Marsupialla: Petauridae) at Bombala, New South Wales. Aust Mammal 9: 17-25.

Hoye, G. A. & Richards, G. C. (1995). Greater Broad-nosed Bat. pp. 527 - 528 in The Mammals of Australia by Strahan, R. (ed). Australian Museum and Reed Books, Sydney.

Kavanagh, R.P. 1987. Forest phonelogy and its effect on foraging behaviour and selection of habitat by the yellow-bellied glider, Petaurus australis. Aust. Wild. Res. 14: 371-84.

Kavangh, R.P. 1987b. Foraging behavious of the yellow-bellied glider, Petaurus australis, near Eden New South Wales. Aust. Mammal. 10:37-39.

Kavanagh, R. P. & Murray, M. (1996). Home range, habitat and behaviour of the Masked Owl Tyto novaehollandiae near Newcastle, New South Wales in Emu 96., pp. 250 - 257.

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Lumsden, L. F. & Menkhorst, P. W. (1996). Yellow-bellied Sheathtail Bat. pp. 161 - 162 in Mammals of Victoria - distribution, ecology and conservation by Menkhorst, P. W. (ed.). Oxford University Press, Melbourne

Lunney, D. (1995) White-footed Dunnart Sminthopsis leucopus. Pp. 143-5 in Strahan, R. (ed.) The Mammals of Australia. Reed Books, Sydney.

Martin, R. W. & Handasyde, K. A. (1995). Koala. pp. 196 - 198 in The Mammals of Australia by Strahan, R. (ed). Australian Museum and Reed Books, Sydney

Menkhorst, P. (1995) White-footed Dunnart Pp. 63-4 in Menkhorst, P.W. (ed.) The Mammals of Victoria: distribution, ecology and conservation. Oxford University Press, Melbourne.

Menkhorst, P. and Knight, F. (2001) A Field Guide to the Mammals of Australia. Oxford Uni Press, Melbourne.

Parnaby, H. A. (1992). An Interim Guide to Identification of Insectivorous Bats of South-eastern Australia. Technical Report No. 8. Australian Museum, Sydney.

Parry-Jones, K. & G. Wardle (2004). A sink or source? - The Grey-headed Flying-fox, Pteropus poliocephalus at an urban colony site. Lumsden, L. & G. Ford, eds. 11th Australasian Bat Conference, Toowoomba 13th-16th April 2004, Program and Abstracts. Australasian Bat Society Newsletter.

Phillips, W. R. (1990). Koalas - the little Australians we would all hate to lose.

Webb, N. & C. Tidemann (1995). Hybridisation between black (Pteropus alecto) and grey-headed (P.poliocephalus) flying-foxes (Megachiroptera: Pteropodidae). Australian Mammalogy. 18:19-26.

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Appendix G Biobanking assessment G.1 Site value scores Map Unit 1: Silvertop Ash - Blue-leaved Stringybark - Woollybutt shrubby open forest on coastal foothills central South East Corner

Site Plot 17 SCORE WT

Native Plant Species Richness 41 3 25

Native Over-storey Cover (%) 21.5 3 10

Native Mid-storey Cover (%) 25 3 10

Native Ground Cover-grasses (%) 20 3 2.5

Native Ground Cover-shrubs (%) 8 3 2.5

Native Ground Cover-other (%) 12 2 1.66

Exotic Plant Cover (%) 0 3 5

Number of Trees with Hollows 1 2 13.33

Over-storey Regeneration 0.3 1 4.17

Total Length of Fallen Logs (m) 95 3 10

Total Score 84.16

Condition H

Map Unit 2: Coast Grey Box - Mountain Grey Gum - stringybark moist shrubby open forest in coastal gullies, southern South East Corner

Site Plot 15

SCOR E WT

Plot 18

SCOR E WT

Plot 21

SCOR E WT

Native Plant Species Richness 6 3 25 0 3 25 42 3 25

Native Over-storey Cover (%) 42 2 6.66 36 3 10 39.5 3 10

Native Mid-storey Cover (%) 0 3 10 0 3 10 7.5 3 10

Native Ground Cover-grasses (%) 1 3 2.5 0 3 2.5 46 3 2.5

Native Ground Cover-shrubs (%) 0 3 2.5 0 2 1.66 10 3 2.5

Native Ground Cover-other (%) 94 3 2.5 28 3 2.5 10 3 2.5

Exotic Plant Cover (%) 0 3 5 0 3 5 0 3 5

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Site Plot

15

SCOR

E WT

Plot

18

SCOR

E WT

Plot

21

SCOR

E WT

Number of Trees with Hollows 2 3 20 0 0 0 1 2 13.33

Over-storey Regeneration 41 3 12.5 23 1 4.16 1 3 12.5

Total Length of Fallen Logs (m) 21.5 3 10 26.5 3 10 68 2 6.66

Total Score 96.66 70.82 89.99

Condition V-H H H

Map Unit 3: Mountain Grey Gum - Yellow Stringybark moist shrubby open forest in gullies of the coastal ranges, northern South East Corner

Site Plot 16 SCORE WT Plot 23 SCORE WT

Native Plant Species Richness 47 3 25 40 3 25

Native Over-storey Cover (%) 31 3 10 23.5 3 10

Native Mid-storey Cover (%) 2 2 6.66 16 3 10

Native Ground Cover-grasses (%) 32 3 2.5 6 3 2.5

Native Ground Cover-shrubs (%) 6 3 2.5 0 0 0

Native Ground Cover-other (%) 42 3 2.5 82 2 1.67

Exotic Plant Cover (%) 0 3 5 0 3 5

Number of Trees with Hollows 1 2 13.33 2 2 20

Over-storey Regeneration 0 0 0 0.66 2 8.25

Total Length of Fallen Logs (m) 94 3 10 55 2 6.66

Total Score 77.49 89.08

Condition H H

Map Unit 4: River Peppermint - Rough-barked Apple moist open forest on sheltered sites, southern South East Corner


Native Plant Species Richness 23 2 16.66

Native Over-storey Cover (%) 26.5 3 10

Native Mid-storey Cover (%) 50 2 6.66


311


Native Ground Cover-shrubs (%) 0 0 0



Number of Trees with Hollows 0 0 0

Over-storey Regeneration 0 0 0

Total Length of Fallen Logs (m) 28 1 3.33

Total Score 44.98

Condition M

Map Unit 5: River Peppermint - Rough-barked Apple - River Oak herb/grass riparian forest of coastal lowlands, southern Sydney Basin and South East Corner


Native Plant Species Richness 49 3 25

Native Over-storey Cover (%) 9 2 6.66

Native Mid-storey Cover (%) 34.5 1 3.33


Native Ground Cover-shrubs (%) 12 2 1.67



Number of Trees with Hollows 0 0 0

Over-storey Regeneration 0 0 0

Total Length of Fallen Logs (m) 45 3 10

Total Score 56.66

Condition M-H

NOTE:

0 to 16 low

17 to 33 low-moderate

34 to 50 moderate

51 to 67 moderate-high

68 to 84 high

85 - 100 very high

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G.2 Biobanking scoring system

Scoring and weighting of the site attributes (adapted from Table 3. of Seidel and Briggs 2008).

Site Attribute Site Attribute Score (see notes below) Weighting for site 0 1 2 3 attribute score

Native Plant Species Richness

0 >0 – <50% of benchmark

50–<100% of benchmark

≥ benchmark 25

Native Over-storey Cover (%)

0–10% or >200% of benchmark

>10–<50% or >150–200% of benchmark

50–<100% or >100–150% of benchmark

within benchmark

10

Native Mid-storey Cover (%)


>10–<50% or >150–200% of benchmark

50–<100% or >100–150% of benchmark

within benchmark

10

Native Ground Cover-grasses (%)


>10–<50% or >150–200% of benchmark

50–<100% or >100–150% of benchmark

within benchmark

2.5

Native Ground Cover-shrubs (%)


>10–<50% or >150–200% of benchmark

50–<100% or >100–150% of benchmark

within benchmark

2.5

Native Ground Cover-other (%)

0– 10% or >200% of benchmark

>10–<50% or >150–200% of benchmark

50–<100% or >100–150% of benchmark

within benchmark

2.5

Exotic Plant Cover (%)

>66% >33–66% >5–33% 0–5% 5

Number of Trees with Hollows

0 (unless benchmark includes 0)

>0–<50% of benchmark


≥ benchmark 20

Proportion of over-storey species occurring as regeneration

0 >0–<50% 50–<100% 1 12.5

Total Length of Fallen Logs (m)

0–10% of benchmark

>10–<50% of benchmark


≥ benchmark 10

Note:

The term ‘within benchmark’ means a measurement that is within (and including) the range of measurement identified as the benchmark for that vegetation type. The term ‘<benchmark’ means a measurement that is less than the minimum measurement in the benchmark range. The term ‘>benchmark’ means a measurement that is greater than the maximum measurement in the benchmark range.

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Appendix H Koala scat search data Plot No.

Map ref.

Tree No.

Tree Species DBH (cm)

Koala Scats/Age

1 1 1 Eucalyptus muelleriana 68 No




1 1 5 Eucalyptus cypellocarpa 57 No

1 1 6 Eucalyptus saligna x botryoides 36 No




1 1 10 Angophora floribunda 59 No






1 1 16 Eucalyptus sieberi 54 No
















314

5

10

15

20

25

30


Plot No.

Map ref.

Tree No.


Koala Scats/Age




2 2 Eucalyptus saligna x botryoides 46 No

























2 2 Eucalyptus muelleriana 60 No





315


Plot No.

Map ref.

Tree No.


Koala Scats/Age































4 4 5 Acacia floribunda 17 No



316


Plot No.

Map ref.

Tree No.


Koala Scats/Age



























5 5 4 Eucalyptus agglomerata 16 No







317


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































318


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































319


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































320


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































321


Plot No.

Map ref.

Tree No.


Koala Scats/Age






















10 14 14 Allocasuarina littoralis 25 No












322


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































323


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































324

5

10

15

20

25

30


Plot No.

Map ref.

Tree No.


Koala Scats/Age




13 15 Eucalyptus agglomerata 25 No





13 15 Eucalyptus sieberi 37 No

























325


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































326


Plot No.

Map ref.

Tree No.


Koala Scats/Age



























16 19 4 Eucalyptus globoidea 37 No







327


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































328


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































329


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































330


Plot No.

Map ref.

Tree No.


Koala Scats/Age


































331


Plot No.

Map ref.

Tree No.


Koala Scats/Age









332

appendix k - part c · ), wild yellow jasmine (pittosporum revolutum), narrow-leaved geebung...

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