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Baseline Persistent organic pollutants in marine birds, arctic hare and ringed seals near Qikiqtarjuaq, Nunavut, Canada Mark L. Mallory a, * , Birgit M. Braune b , Mark Wayland c , Ken G. Drouillard d a Canadian Wildlife Service, P.O. Box 1714, Iqaluit, NU, Canada X0A 0H0 b Canadian Wildlife Service, NWRC, Raven Road, Carleton University, Ottawa, ON, Canada K1A 0H3 c Canadian Wildlife Service, 115 Perimeter Road, Saskatoon, SK, Canada S7N 0X4 d Great Lakes Institute for Environmental Research, University of Windsor, 401 Sunset Avenue, Windsor, ON, Canada N9B 3P4 The contamination of Canadian Arctic marine wild- life by persistent organic pollutants (POPs) has been known since the early 1970s (reviewed in Muir et al., 1992, 1999; Jensen et al., 1997; AMAP, 1998). These compounds typically arrive via long range transport from source areas in tropical or temperate regions, and are deposited in the Arctic by condensing, cool, polar air (Bright et al., 1995; Jensen et al., 1997). Once assimilated into the lower parts of marine food chains, these lipophilic compounds biomagnify with increasing trophic level, and can reach concentrations in top pred- ators that can be deleterious to reproduction or survival (Jensen et al., 1997; Dietz et al., 2000; Borga ˚ et al., 2001; Bustnes et al., 2003). After the initial discovery of POPs in Arctic wildlife (once thought to be too distant from sources to be pol- luted), monitoring programs were established to track contaminant levels in various wildlife groups. Because they are long-lived, forage over large areas, and are often colonial and thus easy to sample, marine birds integrate many aspects of local marine ecosystem condi- tions and have proven to be particularly effective bio- indicators of marine pollution (e.g. Braune et al., 2002). In the Canadian Arctic, concentrations of many POPs in marine birds decreased from the 1970s through the 1980s, and then levelled off by the 1990s (Muir et al., 1999; Braune et al., 2001). Despite a general pattern of decline, however, there remain clear regional differences, with some sites continuing to support wildlife with con- siderably higher contaminant concentrations than other locales (Muir et al., 1999; Braune et al., 2002). Many gaps remain in our geographic knowledge of contami- nant levels in Arctic wildlife tissues. Contamination of Arctic wildlife has been a key con- cern to Inuit (the aboriginal residents of the Canadian Arctic), because harvest of wild animals is the principal source of meat and an important cultural activity (Jen- sen et al., 1997). During our seabird research near two large colonies southeast of Qikiqtarjuaq (formerly Broughton Island), Nunavut (Fig. 1) on eastern Baffin Island, the community expressed concern over possible contamination of wildlife near the colonies, which were located close to two former military sites (Durban and Padloping islands). To address community concerns, evaluate the possibility of point-source contamination in the local marine food chain, and fill in a large geo- graphic gap for contaminant data in Nunavut, we Edited by Bruce J. Richardson The objective of BASELINE is to publish short communications on different aspects of pollution of the marine environment. Only those papers which clearly identify the quality of the data will be considered for publication. Contributors to Baseline should refer to ‘Baseline—The New Format and Content’ (Mar. Pollut. Bull. 42, 703–704). * Corresponding author. Tel.: +1 867 975 4637; fax: +1 867 975 4645. E-mail address: [email protected] (M.L. Mallory). www.elsevier.com/locate/marpolbul Marine Pollution Bulletin 50 (2005) 95–104

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Baseline

Persistent organic pollutants in marine birds, arctic hare andringed seals near Qikiqtarjuaq, Nunavut, Canada

Mark L. Mallory a,*, Birgit M. Braune b, Mark Wayland c, Ken G. Drouillard d

a Canadian Wildlife Service, P.O. Box 1714, Iqaluit, NU, Canada X0A 0H0b Canadian Wildlife Service, NWRC, Raven Road, Carleton University, Ottawa, ON, Canada K1A 0H3

c Canadian Wildlife Service, 115 Perimeter Road, Saskatoon, SK, Canada S7N 0X4d Great Lakes Institute for Environmental Research, University of Windsor, 401 Sunset Avenue, Windsor, ON, Canada N9B 3P4

The contamination of Canadian Arctic marine wild-

life by persistent organic pollutants (POPs) has beenknown since the early 1970s (reviewed in Muir et al.,

1992, 1999; Jensen et al., 1997; AMAP, 1998). These

compounds typically arrive via long range transport

from source areas in tropical or temperate regions,

and are deposited in the Arctic by condensing, cool,

polar air (Bright et al., 1995; Jensen et al., 1997). Once

assimilated into the lower parts of marine food chains,

these lipophilic compounds biomagnify with increasingtrophic level, and can reach concentrations in top pred-

ators that can be deleterious to reproduction or survival

(Jensen et al., 1997; Dietz et al., 2000; Borga et al., 2001;

Bustnes et al., 2003).

After the initial discovery of POPs in Arctic wildlife

(once thought to be too distant from sources to be pol-

luted), monitoring programs were established to track

contaminant levels in various wildlife groups. Becausethey are long-lived, forage over large areas, and are

often colonial and thus easy to sample, marine birds

integrate many aspects of local marine ecosystem condi-

tions and have proven to be particularly effective bio-

indicators of marine pollution (e.g. Braune et al., 2002).In the Canadian Arctic, concentrations of many POPs

in marine birds decreased from the 1970s through the

1980s, and then levelled off by the 1990s (Muir et al.,

1999; Braune et al., 2001). Despite a general pattern of

decline, however, there remain clear regional differences,

with some sites continuing to support wildlife with con-

siderably higher contaminant concentrations than other

locales (Muir et al., 1999; Braune et al., 2002). Manygaps remain in our geographic knowledge of contami-

nant levels in Arctic wildlife tissues.

Contamination of Arctic wildlife has been a key con-

cern to Inuit (the aboriginal residents of the Canadian

Arctic), because harvest of wild animals is the principal

source of meat and an important cultural activity (Jen-

sen et al., 1997). During our seabird research near two

large colonies southeast of Qikiqtarjuaq (formerlyBroughton Island), Nunavut (Fig. 1) on eastern Baffin

Island, the community expressed concern over possible

contamination of wildlife near the colonies, which were

located close to two former military sites (Durban and

Padloping islands). To address community concerns,

evaluate the possibility of point-source contamination

in the local marine food chain, and fill in a large geo-

graphic gap for contaminant data in Nunavut, we

Edited by Bruce J. Richardson

The objective of BASELINE is to publish short communications on different aspects of pollution of the marineenvironment. Only those papers which clearly identify the quality of the data will be considered for publication.

Contributors to Baseline should refer to ‘Baseline—The New Format and Content’ (Mar. Pollut. Bull. 42, 703–704).

* Corresponding author. Tel.: +1 867 975 4637; fax: +1 867 975

4645.

E-mail address: [email protected] (M.L. Mallory).

www.elsevier.com/locate/marpolbul

Marine Pollution Bulletin 50 (2005) 95–104

sampled marine birds, arctic hare (Lepus arctica) and

ringed seals (Pusa hispida) near Qikiqtarjuaq to deter-mine their POP levels.

Tissue samples were collected 100km southeast of

Qikiqtarjuaq during 10–14 September 2001 (with the

exception of seals, n = 2, collected from local hunters

in October 2001). Target wildlife species were collected

using a 12 gauge shotgun, firing 70mm, #4 steel shot-

shells. The species were chosen to represent a range of

trophic levels or food webs, with glaucous gulls (Larushyperboreus; n = 1) and northern fulmars (Fulmarus gla-

cialis; n = 2) representing top marine predators and

scavengers, black guillemots (Cepphus grylle; n = 8) rep-

resenting nearshore piscivores, common eiders (Somate-

ria mollissima borealis; n = 8) representing benthic

molluscivores, and arctic hare (n = 2) representing

terrestrial herbivores. Most bird samples were of adults,

although one eider and six guillemots were juveniles.Whole carcasses were placed in individual bags, labelled

with the time and location of the collection, and shipped

frozen to Iqaluit where carcasses were partially thawed

to permit measurement and dissection of �5g breast

muscle and liver samples which were wrapped in hex-

ane-rinsed foil, refrozen and shipped to the Great Lakes

Institute for Environmental Research (GLIER) for POP

analyses.POP analyses of sample tissues included determina-

tion of chlorobenzenes (P

CBz = 1,2,4,5-tetrachloroben-

zene, 1,2,3,4-tetrachlorobenzene, pentachlorobenzene

and hexachlorobenzene), hexachlorocyclohexanes

(P

HCH = a-, b-, and c-hexachlorocyclohexane),chlordane-related compounds (

PCHLOR = oxychlor-

dane, trans-chlordane, cis-chlordane, trans-nonachlor,

cis-nonachlor and heptachlor epoxide), DDT and itsmetabolites (

PDDT = p,p0-DDE, p,p0-DDD and

p,p0-DDT), mirex (P

MIREX = photomirex and mirex),

dieldrin, and PCBs (P

PCB = 78 congeners identified

according to IUPAC numbers (Ballschmiter and Zell,

1980): 16/32, 17, 18, 19, 20/33, 22, 24/27, 25, 26, 28, 31,

40, 42, 44, 45, 49, 52, 60, 64, 66/95, 70, 74, 85, 87, 91,

92, 95, 97, 99, 101, 105, 110, 118, 129, 130, 132, 134,

135/144, 136, 137, 138, 141, 146, 149, 151, 153, 156,157, 158, 170/190, 171, 172, 174, 176, 177, 178, 179,

180, 182/187, 183, 185, 194, 195, 199, 200, 201, 202,

203, 206, 207, and 208).

All samples were analyzed according to CAEAL-

accredited standard operating procedures (Environment

Canada, 1989). Chemical extraction and cleanup of

PCBs and organochlorine pesticides followed the proce-

dures of Lazar et al. (1992). Briefly, tissue homogenateswere ground and spiked with 1,3,5-tribromobenzene as a

surrogate recovery standard and extracted with 350ml

of dichloromethane: hexane (50:50% v/v, OmniSolve-

Grade, VWR, ON, Canada). Cleanup of the sample

was performed by gel permeation chromatography fol-

lowed by activated Florisil (VWR, ON, Canada) chro-

matography. Chemical analysis was performed using a

Hewlett-Packard 5890 gas chromatograph with 5973mass selective detector (GC-MSD) and 7673 autosam-

pler. The column was a 60m · 0.250mm · 0.1lm DB-

5 (Chromatographic Specialties, Brockville, ON). For

every batch of five samples injected, the surrogate stand-

ard, PCB standard mixture, organochlorine standard

mixture, method blank and in-house reference tissue

also were analyzed. PCBs were quantified according to

the method described by Drouillard and Norstrom(2003). Detection limits ranged from 0.01 to 0.08ng/g

wet weight depending on the chemical of study. Blanks

and reference tissues, quantified during each batch of

sample extractions, were in compliance with the normal

quality assurance procedures instituted by GLIER’s

CAEAL certified organic analytical laboratory. Sample

recoveries for the surrogate standard averaged 89 ± 2%

(mean ± SE). Chemical concentrations were not recov-ery corrected.

We loge-transformed data to approximate normal

distributions, and then used t-tests with Bonferroni cor-

rection to compare concentrations of POPs in tissues of

various species. The following PCB congeners were not

detected in any bird or hare samples: PCB 19, 24/27, 22,

25, 45, 40, 42, 199. In seals, PCBs 19, 40, 132, 176, 199,

200, 207 were not detected; seal fat samples had detect-able levels of all 71 other congeners. Dieldrin was not

detected in eider, hare or seal muscle, nor in seal liver.

Mirex was not detected in eider or seal liver, nor hare

muscle. All fulmar and gull tissues, as well as seal fat,

had detectable levels of all POP residues examined.

Compared to the marine species, concentrations of most

POPs in arctic hare were low. In guillemots, eiders and

seals, POP concentrations were typically higher in livertissue than in muscle, but this pattern was reversed in

the fulmars and glaucous gull (Table 1).

Fig. 1. Location of the study area in eastern Arctic Canada (black

circles denote former military sites, star denotes community of

Qikiqtarjuaq). Gray areas on the Cumberland Peninsula represent

glaciers.

96 Baseline / Marine Pollution Bulletin 50 (2005) 95–104

Table 1

Geometric means ± SD and ranges (in brackets) in ng/g wet wt. as well as lipid-normalized means ± SD (ng/g) of POPs in muscle and liver tissues of wildlife from the Qikiqtarjuaq area

Mean ± SD (Range) Species tissue (n)

Black guillemot (8) Common eider (8) Northern fulmar (2) Glaucous gull

(1)

Arctic hare (2) Ringed seal (2)

Muscle Liver Muscle Liver Muscle Liver Muscle Liver Muscle Muscle Liver Fat

% Lipid 2.46 ± 0.41 2.84 ± 1.64 1.75 ± 0.67 1.99 ± 0.46 8.10 6.12 5.43 2.74 2.36 2.76 3.10 97.9

(1.88–3.01) (1.27–6.18) (0.78–2.48) (1.29–2.44) (5.25, 10.95) (3.39, 8.85) – – (2.32, 2.40) (1.82, 3.67) (2.81, 3.38) (95.3, 100.7)P

PCB 27.00 ± 36.34 34.71 ± 56.33 2.73 ± 1.64 5.32 ± 6.46 38.21 30.12 560.4 219.6 7.95 7.58 14.51 804.6

(8.36–100.93) (5.90–172.52) (0.58–5.70) (0.43–19.33) (20.21, 56.21) (14.00, 46.25) – – (0.11, 15.80) (6.08, 9.08) (6.70, 22.33) (302.8, 1306)

975 ± 1793 1494 ± 2508 152 ± 65 276 ± 316 449 468 10,320 8013 343 327 449 808P

DDT 3.32 ± 2.52 6.51 ± 4.16 1.36 ± 0.83 1.40 ± 0.71 29.19 19.60 291.8 116.8 0.05 4.52 4.66 491.4

(0–6.93) (2.38–13.53) (0.14–2.72) (0.28–2.31) (17.81, 40.56) (9.30, 29.90) – – (0, 0.10) (3.01, 6.04) (1.79, 7.54) (236.9, 745.8)

143 ± 120 264 ± 176 79 ± 35 77 ± 37 355 306 5374 4263 2.1 203 143 495P

CHLOR 2.89 ± 2.63 7.00 ± 4.38 0.99 ± 0.82 4.50 ± 3.80 17.12 20.95 66.29 39.76 0.12 2.77 8.31 509.2

(0–7.34) (3.36–15.18) (0–2.64) (0.68–11.37) (9.57, 24.66) (15.33, 26.57) – – (0, 0.23) (2.68, 2.85) (3.89, 12.72) (250.9, 767.4)

126 ± 131 285 ± 184 60 ± 39 227 ± 150 204 376 1221 1451 5.0 113 257 513

Dieldrin 0.23 ± 0.64 2.71 ± 1.03 0 3.30 ± 1.87 6.53 11.26 3.28 1.99 0 0 0 58.03

(0–1.82) (1.72–4.05) – (1.90–7.00) (3.76, 9.29) (8.20, 14.32) – – – – – (57.68, 58.39)

12 ± 34 51 ± 70 0 133 ± 102 78 202 60 73 0 0 0 59P

MIREX 0.16 ± 0.28 0.44 ± 0.47 0.01 ± 0.02 0 1.01 0.85 15.33 8.88 0 0.63 0 13.86

(0–0.70) (0–1.37) (0–0.04) – (0.51, 1.50) (0.17, 1.53) – – – (0.54, 0.72) – (3.44, 24.28)

8 ± 14 18 ± 21 0.2 ± 0.6 0 12 11 282 324 0 27 0 14P

CBz 3.06 ± 2.20 6.90 ± 3.67 1.37 ± 0.92 1.56 ± 0.85 14.26 10.84 22.62 13.57 0.06 0.59 0.56 33.43

(0–5.35) (3.66–14.34) (0.10–3.17) (0.64–3.27) (9.62, 18.90) (6.35, 15.33) – – (0.02, 0.10) (0.48, 0.70) (0.44, 0.67) (28.65, 38.21)

130 ± 103 270 ± 113 80 ± 41 84 ± 35 178 180 417 495 2.6 22 18 34P

HCH 1.41 ± 1.11 2.58 ± 1.59 0.42 ± 0.44 1.63 ± 1.67 0.70 0.52 2.67 1.25 0 0.85 0.91 32.61

(0–2.61) (0.98–5.09) (0–1.06) (0.44–4.93) (0.46, 0.94) (0.28, 0.76) – – – (0.52, 1.18) (0.72, 1.10) (30.62, 34.60)

60 ± 51 105 ± 65 26 ± 28 69 ± 64 9 8 49 45 0 30 29 33

Baselin

e/Marin

ePollu

tionBulletin

50(2005)95–104

97

Among all wildlife, contaminant concentrations (ex-

pressed in ng/g wet weight) were considerably higher

in seal fat than in all other tissues (Table 1). Considering

only muscle and liver tissues, the glaucous gull had the

highest concentration of all POPs examined, except for

dieldrin (highest in fulmar tissues) andP

HCH (highestin guillemot livers). Concentrations of

PPCB,

PDDT,P

CHLOR andP

MIREX increased following this pat-

tern: eider < guillemot < fulmar < gull. Fulmars, how-

ever, had higher dieldrin and lowerP

HCH levels than

the glaucous gull. The glaucous gull had the highest con-

taminant burdens for all residues except dieldrin (high-

est in fulmars) andP

HCH (highest in guillemots)

when comparing lipid-normalized values of POPs.One outlier was found among the samples, an adult

common eider, which was excluded from the analyses

above and Table 1. For this bird,P

PCB was 5487ng/g

wet wt. in muscle and 4173ng/g wet wt. in liver (approx-

imately 1000 times higher than the next closest eider).

Most of the detectable PCB congeners were elevated in

this specimen, but PCBs 55, 105, 118, 156, 157, 183,

187, and particularly 138, 146, 153, 170/190, 180, 187and 194 were detected at much higher levels than in

the other eiders. Other POPs, however, were in the same

range as the rest of the eiders.

Concentrations of POPs in muscle tissue of black

guillemots and common eiders were similar (all

P > 0.05; Table 1). In liver tissues, concentrations ofPCBz and

PDDT were significantly higher in guille-

mots (P < 0.01; Table 1), while other POP levels didnot differ significantly between the species. The propor-

tional contribution of various PCB congeners to thePPCB also differed among species (Fig. 2).

PPCB in

black guillemot had relatively similar contributions

from congeners 105, 118, 138 and 153 whereas, in the

other birds, PCB 153 was the dominant congener fol-

lowed by PCB 138, with lower contributions (<7%) from

PCB 105. Ringed seals had higher proportions of lower-chlorinated PCB congeners than the other species, while

arctic hare had higher proportions of the hepta- and

octachlorobiphenyls (Table 2), but also from specific

PCBs 87, 110 and 149. Guillemots also differed from

the other birds by having high proportions of both

penta- and hexachlorobiphenyls.

For the suite of POPs examined, almost all residue

concentrations in muscle and livers of wildlife fromQikiqtarjuaq were below levels thought to be of concern

for wildlife health (Kamrin and Ringer, 1996; Weime-

yer, 1996; Braune et al., 1999a; Muir et al., 1999). Ex-

cept for the possibility of the single common eider

outlier identified above, there was no evidence of

point-source contamination for POPs in the local mar-

ine environment, nor of trace elements (Mallory et al.,

2004), and therefore local breeding marine birds donot appear to be contaminated from wastes at the for-

mer local military sites.

Seabird concentrations of PCBs were lower than

most species studied in the North Pacific and Southern

Oceans (Guruge et al., 2001), and most of the POPs

examined in this study were lower than other sites in

the eastern Arctic (Braune et al., 1999a,b; Buckman

et al., 2004), and were much lower than those measuredat sites known to be affected by point-source contamina-

tion (e.g. Connell et al., 2003) or at levels known to be

lethal or deleterious to birds (Weimeyer, 1996).

Glaucous gulls are a top predator in Arctic marine

ecosystems, and typically accumulate high contaminant

burdens (e.g. Savinova et al., 1995; Muir et al., 1999;

Skaare et al., 2000; Braune et al., 2002). The gull sam-

pled at Qikiqtarjuaq hadP

PCB,P

CHLOR,P

DDTand

PMIREX concentrations in breast muscle that

were approximately ten times lower than values found

at some other sites in the eastern Arctic (Braune et al.,

1999b). It also had POP concentrations similar to lower

levels found for glaucous gulls at Ny-Alesund and Bjør-

nøya (Savinova et al., 1995), particularly for PCBs. In

general, concentrations of POPs are much higher in gulls

of the Barents Sea than in the Canadian Arctic (e.g.,Henriksen et al., 2000; Braune et al., 2002; Buckman

et al., 2004).

For guillemots, samples from Qikiqtarjuaq also had

POP concentrations about 10 times lower than found

elsewhere in eastern Arctic (Braune et al., 1999b), and

similar to values from Greenland birds (Vorkamp

et al., 2004), butP

PCBs andP

CHLOR in young guil-

lemots were similar to those in nestling black guillemotsfrom an uncontaminated site in Labrador (Kuzyk et al.,

2003). Hexachlorocyclohexanes (P

HCH) were higher in

guillemots from Qikiqtarjuaq compared to those from

Iceland (Olafsdottir et al., 2001), and similarlyP

PCB,

DDT and dieldrin were higher in Qikiqtarjuaq guille-

mots than those collected in western Hudson Bay (John-

stone et al., 1996). This suggests that Qikiqtarjuaq

guillemots, or perhaps guillemots inhabiting the easternArctic coastline along Baffin Island and northern Labra-

dor, may be relying on different foods than those from

the other regions, and may be wintering in areas exposed

to higher concentrations of these contaminants.

Eiders at Qikiqtarjuaq had POP concentrations lower

than those typically found in Maritime Canada, but

consistent with values from across the eastern Arctic

(Braune et al., 1999b). Compared to the European Arc-tic, concentrations of

PCBz were similar, but Qikiqtar-

juaq eiders had higher concentrations ofP

HCH, lower

concentrations ofP

PCB andP

CHLOR, and much

lower concentrations ofP

DDT (Savinova et al.,

1995). Concentrations ofP

PCB and DDT in eiders

from Iceland (Olafsdottir et al., 2001) were higher than

those found in the Qikiqtarjuaq birds. The exception

to these patterns is the outlier eider, which hadP

PCBconcentrations higher than any reported in the studies

above. The liverP

PCB concentration in this eider

98 Baseline / Marine Pollution Bulletin 50 (2005) 95–104

was in the range of values found for guillemots from a

contaminated former military site in Newfoundland,

Canada (Kuzyk et al., 2003) where negative physiologi-

cal responses were observed. The effect of PCB concen-

trations on birds varies by species (Hoffman et al., 1996),

and it is not known what levels may be harmful to

Fig. 2. Distribution of PCB congeners representing at least 2% of the Total PCBs in muscle tissue of at least one species examined. Species were as

follows: BLGU––black guillemot; NOFU––northern fulmar; GLGU––glaucous gull; COEI––common eider; ARHA––arctic hare; RISE––ringed

seal.

Table 2

Proportional contribution of PCB congeners by chlorination group in muscle tissue of examined species

Chlorination group Proportion of total PCB burden (%)

Black guillemot Common eider Northern fulmar Glaucous gull Arctic hare Ringed seal

Trichlorobiphenyls 0.5 1.1 1.6 0.1 0.2 3.3

Tetrachlorobiphenyls 6.4 7.5 12.7 3.1 3.9 17.5

Pentachlorobiphenyls 41.1 22.3 27.6 17.5 26.6 40.5

Hexachlorobiphenyls 41.3 53.5 41.5 53.3 40.3 32.5

Heptachlorobiphenyls 9.7 15.1 14.0 22.1 24.1 6.2

Octachlorobiphenyls 1 0.5 2.1 3.5 4.5 0

Nonachlorobiphenyls 0 0 0.5 0.4 0.4 0

Baseline / Marine Pollution Bulletin 50 (2005) 95–104 99

eiders. It is possible that high PCB levels in this bird

resulted from it feeding in a very localized area of

PCB pollution at one of the former military sites (e.g.,

Kuzyk et al., 2003). However, the fact that this was an

adult bird, and that none of the other local wildlife

had concentrations within an order of magnitude of thisspecimen suggests that the contaminants were acquired

during migration or wintering.

The ringed seals sampled at the site had POP concen-

trations within ranges reported elsewhere in the Cana-

dian Arctic; somewhat lower than reported for western

Hudson Bay and southwestern Ellesmere Island, but

higher than Amundsen Gulf and Barrow Strait (Muir

et al., 1999). PCB, DDT and CBz concentrations weresimilar in Qikiqtarjuaq seals to ringed seals sampled in

Alaska, but Alaskan seals had much higher levels of

HCH (Kucklick et al., 2002). However, Hoekstra et al.

(2003) found very similar lipid-normalized concentra-

tions of PCB, DDT, CHLOR and HCH in 20 seals in

the Beaufort-Chukchi Seas as we observed near Qikiq-

tarjuaq. The two seals sampled in this study differed in

PCB concentrations by a factor of four; male seals areknown to accumulate considerably higher POP concen-

trations than females (Muir et al., 1999), and that may

explain the differences at Qikiqtarjuaq.

PCB congeners 153 and 138 dominated the PCB con-

gener pattern in all species at Qikiqtarjuaq (Fig. 2). In

the eiders, fulmars and the gull, PCBs 153, 138, 180

and 118 were found in the highest concentrations and

therefore contributed the highest proportions toP

PCB(Fig. 2). A similar pattern has been found in other sea-

birds from disparate regions around the world (e.g.,

Focardi et al., 1989; Klasson-Wehler et al., 1998; Gur-

uge et al., 2001; Buckman et al., 2004). The proportional

contribution of each congener to the overall PCB burden

clearly differed across species at Qikiqtarjuaq (Fig. 2),

which has also been shown in Iceland (Olafsdottir et al.,

2001). Differences in the proportional distribution ofPCB congeners among species may be attributable in

part to exposure and uptake, but also to differential

metabolic capabilities for dealing with these chemicals,

particularly between birds and mammals (e.g., Fisk

et al., 2001; Ruus et al., 2002a,b). The major PCB con-

geners measured in birds are characteristically blocked

at meta–para-sites along both phenyl rings and thus

are not expected to undergo significant biotransforma-tion (Drouillard and Norstrom, 2003).

Organochlorine contaminants biomagnify up food

chains, and particularly marine food chains, because

they are longer than terrestrial chains and because mar-

ine animals are relatively high in lipids, a tissue to

which organochlorines readily bind (Muir et al., 1992;

Dietz et al., 2000; Ruus et al., 2002b). Near Qikiqtarjuaq,

POP concentrations generally increased from eiders toguillemots to fulmars to gulls, notably in the lipid-nor-

malized values, and representing as much as a 100-fold

amplification. Similar patterns in POP concentrations

among marine bird trophic webs have been observed

in other studies (Savinova et al., 1995; Borga et al.,

2001; Braune et al., 2002). The main exception to this

pattern was the result forP

HCH, which did not bio-

magnify appreciably at this site. This is consistent withresults from Iceland (Olafsdottir et al., 2001) and else-

where (Muir et al., 1999), and may be attributable to

the ability of birds to metabolize these substances as well

as the physical and chemical properties of HCHs, which

do not favour biomagnification (e.g., relatively low

octanol–water partition coefficient compared to other

organochlorines).

Most marine birds collected near Qikiqtarjuaq, east-ern Baffin Island, Canada, showed no evidence of high,

point source POP contamination; rather most measured

concentrations were lower than or consistent with back-

ground levels over much of the Canadian Arctic. Even

the one eider with higher PCB concentrations was well

below levels associated with health concerns. With the

exception of glaucous gulls, these levels appear to pose

little threat for the long-term health of these species.However, recent evidence suggests that contaminants

not addressed in this study, such as brominated flame

retardants, may be increasing (Braune, 2003), and thus

monitoring levels in birds of this region may prove

warranted.

Acknowledgments

Many thanks to J. Noble Jr., J. Aliqatuqtuq, J.

Nookiguak, D. Pickle, J. Akearok, and A. Fontaine

for assistance with aspects of this study. Financial sup-

port was provided by Environment Canada (CWS)

and Indian and Northern Affairs Canada, Northern

Contaminants Program (Local Contaminant Concerns).

This study was conducted under permits NUN-SCI-01-02, WRP 000140, and SRL 0100401N-A.

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Polycyclic aromatic hydrocarbons in capelin (Mallotus villosus) in theBarents Sea by use of fixed wavelength fluorescence measurements

of bile samples

C. Haugland a,*, K.I. Ugland a, J.F. Børseth b, E. Aas b

a Section of Marine Biology and Limnology, University of Oslo, P.O. Box 10634, Blindern, 0316 Oslo, Norwayb RF-Rogaland Research, P.O. Box 2503, Ullandhaug, N-4091 Stavanger, Norway

Polycyclic aromatic hydrocarbons (PAHs) are pres-

ent in most marine and terrestrial habitats. Some PAH

molecules have been shown to possess mutagenic and

carcinogenic effects on organisms (Varanasi et al.,

1989; Kurelec, 1993). Other damaging effects includeskin lesions, skeletal deformities and tumours (Krahn

et al., 1986; Malins et al., 1988; Collier and Varanasi,

1991; Hose et al., 1996; Baumann, 1998). PAHs in the

environment derive primarily from two different

sources: (1) pyrogenic molecules that are formed during

incomplete combustion of organic material, and (2)

petrogenic molecules that are components of fossil fuels

(Varanasi et al., 1989). Petrogenic PAHs are of increas-ing concern in the marine environment due to oil explo-

ration and transport. The Barents Sea is a productive

ocean in the Arctic climate zone (Fig. 1) located between

northern Norway, Svalbard and Novaja Zemlja (Loeng,

1991). In the southeast Barents Sea, the Norwegian oil

company Statoil is developing a large gas field called

Snøhvit.

The field was discovered in 1984 and is planned to beoperational in 2006. Statoil conducts several environ-

mental baseline investigations in the southern Barents

Sea. The purpose of this study was to determine the lev-

els of PAH in capelin by use of fixed wavelength fluores-

cence (FF). Capelin (Mallotus villosus Muller) is a small

coldwater species with a northern circumpolar distribu-

tion. Capelin is a key species in the Barents Sea since it is

the main food source for marine mammals, seabirds andlarger fish species like cod (Gjøsæter, 1998). This species

is therefore a natural choice in a monitoring program.

PAH compounds can be absorbed by organisms by

ingestion, diffusion through surfaces or by gas exchange

(Varanasi et al., 1989). After the molecules are taken up

by fish they are biotransformed into polar metabolites,

and thereby enhance the efficiency of excretion (Lawand Klungsøyr, 2000). The metabolites are concentrated

in the gall bladder. Sensitive measurements of PAHs

may therefore be based on samples from the bile (Aas

et al., 2000; Jonsson et al., 2004).

Sampling of capelin was carried out in 2002 at two

different locations. On April 13th, 50 individuals were

taken (15 males and 35 females) at location 1

(70�530N; 29�240E). On April 17th, 18 individuals, allmales, were caught at location 2 (70�520N; 29�290E)(Fig. 1). The fish were kept alive in tanks with running

water. Dead fish were not used for further analysis.

From each individual, the gall bladder was removed

and stored in cryo-tubes frozen in liquid nitrogen for

shipment.

The fluorescence analyses were conducted according

to Aas et al. (2000) using a Perkin Elmer LS50B lumi-nescence spectrofluorometer. This method is considered

to be semi-quantitative and semi-qualitative due to lack

of absolute values of the different PAH metabolites.

Thus the measurements only provide an indication of

exposure, but the advantages are that relatively large

samples can be analysed at a low cost (Aas et al.,

2000). The method uses wavelength pairs for excited

and emitted light as a result of the ability of PAH mol-ecules to absorb ultraviolet light followed by emission of

light of a longer wavelength.

The bile samples were analysed at the wavelength

pairs 290/335, 341/383 and 380/430 nm, optimised for

the detection of naphthalene, pyrene and benzo[a]pyrene

type metabolites (Krahn et al., 1987; Lin et al., 1996;

0025-326X/$ - see front matter Crown Copyright � 2004 Published by Elsevier Ltd. All rights reserved.

doi:10.1016/j.marpolbul.2004.10.029

* Corresponding author. Tel.: +47 986 38 786; fax: +47 22854438.

E-mail addresses: [email protected], [email protected]

(C. Hauglnad).

102 Baseline / Marine Pollution Bulletin 50 (2005) 95–104