Lead, cadmium, mercury and selenium in Greenland marine biota and sediments during AMAP phase 1

The Science of the Total Environment 245 Ž2000. 3]14

Lead, cadmium, mercury and selenium in Greenland marine biota and sediments during AMAP phase 1 F. RigetU , R. Dietz, P. Johansen, G. Asmund Ministry of En¨ ironment and Energy, National En¨ ironmental Research Institute, Department of Arctic En¨ ironment, Tagens¨ ej 135, 4 floor, DK-2200 Copenhagen, Denmark Received 8 July 1999; accepted 11 July 1999

Abstract Lead, cadmium, mercury and selenium levels in the Greenland marine environment from the first phase of the AMAP are presented. Samples were collected in 1994]1995 covering four widely separated regions in Greenland. Samples included sediments, soft tissue of blue mussel; and liver of polar cod, shorthorn sculpin, glaucous gull, Iceland gull and ringed seal. Concentrations of lead were found to increase with the size of blue mussel, but not with the age of gulls or ringed seal. Both cadmium and mercury concentrations were found to increase with the sizerage of all species. Selenium concentrations decreased with increasing size of blue mussel, but increased with the age of gulls and ringed seal. Element levels found are within the range of those found in previous studies in Greenland. Relative to global background levels, lead levels must be considered low, whereas levels of cadmium, mercury and selenium in Greenland marine biota are high. Significant differences in element levels in sediments and biota among regions in Greenland were seen in several cases. There was a tendency for the highest lead and mercury concentrations to be found in east Greenland, whereas the highest cadmium concentrations were found in central west Greenland. However, the geographical differences among the media did not show a consistent pattern. Q 2000 Elsevier Science B.V. All rights reserved. Keywords: Lead; Cadmium; Mercury; Selenium; Greenland; Marine biota; Sediments; AMAP

U

Corresponding author.

0048-9697r00r$ - see front matter Q 2000 Elsevier Science B.V. All rights reserved. PII: S 0 0 4 8 - 9 6 9 7 Ž 9 9 . 0 0 4 2 9 - 5

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F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

1. Introduction In 1991 the eight-circumarctic nations established the Arctic Environmental Protection Strategy. The participants agreed to develop an Arctic Monitoring and Assessment Program ŽAMAP. to establish an international monitoring network for the region. The purpose of the Greenland programme was to collect marine sediment, blue mussels, polar cod liver, glaucous gull liver and ringed seal liver from four widely separated regions in Greenland and to compare contaminant levels both within these regions, and with levels found elsewhere in the Arctic. The data obtained have been included in the AMAP assessment of heavy metals within the Arctic ŽDietz et al., 1998a.. Data for lead, cadmium, mercury and selenium in the Greenland marine environment have previously been obtained within other programmes conducted over the past 20 years, in connection with baseline studies of the distribution of elements in Greenland marine ecosystems and monitoring studies of pollution from mining and military activities. These data have been compiled and assessed by Dietz et al. Ž1996. and by Loring and Asmund Ž1996.. This paper presents the results of the Greenland marine component of AMAP, conducted from 1994 to 1995, on levels of lead, cadmium, mercury and selenium in sediments and biota. The paper focuses on the influence of covariates, element levels and geographical differences in element concentrations.

2. Materials and methods 2.1. Sampling and sample preparation The aim of the sampling programme was to collect samples of marine sediments and biota from three locations from west Greenland Žnorth, central and south. and one location from central east Greenland ŽFig. 1.. Samples collected include marine sediments, blue mussel Ž Mytilus edulis., polar cod Ž Boreogadus saida., shorthorn sculpin

Fig. 1. Map of Greenland showing placenames mentioned in the text.

Ž Myoxocephalus scorpius., glaucous gull Ž Larus hyperboreus., Iceland gull Ž Larus glaucoides. and ringed seal Ž Phoca hispida.. Sediment samples were taken by means of a stainless steel core sampler at Qeqertarsuaq and Nanortalik. At Avanersuaq and Ittoqqortoormiit a modified Eckman core sampler was used. Immediately after sampling, the top 1 cm of the sediment cores was removed for analysis. The grain size of the sediments ranged from silt to sand. Samples were frozen in polyethylene plastic bags. Once in the laboratory, sediment samples were freeze dried and stored in air-tight containers. Samples of blue mussel could not be obtained in Avanersuaq and Ittoqqortoormiit as these areas are outside the distribution range of this species. An additional sampling area in Uummannaq was included in the programme to represent the northern extent of the Greenland westcoast distribution range. Mussels were collected by hand at low tide in the intertidal zone at three stations

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

in each area. After sampling the blue mussels were pooled into five 1-cm size categories according to shell length, each normally consisting of approximately 20 individuals. The shells were cut open and allowed to drain before removing the soft parts with a stainless steel scalpel. Individuals contaminated with sediment were discarded. The byssus was not included in the tissue to be analysed. The soft parts were stored frozen at y208C. In the laboratory, the soft parts from each size category were freeze-dried and homogenised prior to analysis. Samples of polar cod were obtained from Avanersuaq and from Ittoqqortoormiit. It was not possible to collect samples from Nanortalik, and the polar cod from Qeqertarsuaq were considered too small for analysis. Samples of shorthorn sculpin were obtained from all four areas. All fish were frozen whole. In the laboratory fish length and sex were recorded, and the liver was removed when the fish were lightly thawed. Stainless steel scalpels, polyethylene gloves and cutting boards were used. Glaucous gulls or Iceland gulls from all four areas were shot by local hunters with a rifle. To avoid contamination, lead ammunition was not used, and wounded tissue was not included in the analyses. All gulls were frozen whole in polyethylene plastic bags. In the laboratory sex, weight and age Žbased on plumage and sexual maturity. were recorded for each gull. Liver samples were removed following the procedure described by Nielsen and Dietz Ž1989.. Ringed seal samples from all four areas were obtained from local hunters. The animals were either shot or caught in nets. Body length, circumference and blubber thickness were recorded, and the canines were collected for later age determination. Samples were placed in polyethylene plastic bags and frozen. In the laboratory, liver samples were lightly thawed so that the outer exposed tissue layer could be cut away to minimise possible contamination and changes due to handling and storage. No particular part of the liver was sampled, since elements are homogeneously distributed within this organ ŽNielsen and Dietz 1990.. The age of the seals was estimated by

5

counting annual layering in the cementum of the canine tooth, following methods described by Dietz et al. Ž1991.. Toluidine blue was used as the staining agent. 2.2. Chemical analysis The analytical methods employed were based on nitric acid digestion of samples followed by element determination using atomic absorption. The quality assurance protocols included the use of certified reference materials, and participation in laboratory performance studies. Both are described in detail by Asmund and Cleemann, 2000. 2.3. Data analysis The statistical analysis were performed with the SAS statistical software package ŽSAS, 1990.. A significance level of Ps 0.05 has been used except where stated otherwise. Trace element concentrations in glacial sediments have been shown to be related to sediment grain size. To compensate for this concentrations have been normalised to those of lithium ŽLoring and Rantala, 1992.. The normalisation was carried out by an analysis of covariance ŽANCOVA. with locality as the main factor and lithium concentration as covariate. The interaction effects were not significant at 5% level in any of the normalisations, meaning that the slope of the relationship between trace element Žcadmium, lead and mercury. did not differ among localities. That is, the plot of trace element vs. lithium concentrations are described as parallel lines, one for each area; the intersection of these lines with the line ‘Li s 22’ are the normalised concentrations. Li s 22 is the overall mean lithium concentration of 22 mgrg dry weight. Comparisons in mean lithium normalised element concentrations between localities were carried out using a pairwise test of least square means ŽLSMEAN. from the ANCOVA. LSMEAN is the estimated mean in each of the localities with the covariate as its mean value. Element concentrations in biota were logarithmically Žbase e. transformed in order to

6

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

meet the assumptions of parametric statistical analysis. Preliminary analysis of element concentrations in biota indicate that there is a linear relationship between the log-transformed element concentrations and length, and that this relationship provides a reasonable description of accumulation in the case of blue mussel, polar cod and shorthorn sculpin. However, the relationships between log-transformed element concentrations and age were not linear for gulls and ringed seals. Element concentrations in soft tissue of blue mussel were analysed with an ANCOVA including a fixed locality factor, a random stationwithin-locality factor and the log-transformed mean shell length as covariate. Interaction factors between locality and shell length and between station-within-locality and shell length were also included. This ANCOVA was then successively reduced for factors not significant at the 5% level according to Type III Sum of Squares test. The final reduced statistical analyses, including only significant factors, were then used to test for differences in mean or normalised mean element concentrations between localities. The normalisation of element concentration according to shell length was performed in cases where there was a significant interaction effect using the localityspecific relationship between element concentrations. In cases with no significant interaction factor, but with a significant relationship between shell length and element concentration, an estimated common relationship was used. Normalised element concentrations were compared between localities by testing of the LSMEAN values. When no influence of shell length on element concentrations was found comparisons of mean element concentrations between localities was performed using the Tukey’s studentised range test. The same principle as described for blue mussel was applied to the data for polar cod and shorthorn sculpin. The first performed ANCOVA included a locality factor and the log-transformed fish length as the covariate, together with the interaction factor between the two factors. As no sex dependency was found for gulls and

ringed seal, sex was not included in further statistical analyses. Cadmium, mercury and selenium concentrations in liver of gulls and ringed seal showed a clear dependency of age, whereas, this was not the case for lead. In order to minimise the influence of age on liver concentrations of cadmium, mercury and selenium in gulls and ringed seal, data were divided into separate age groups; five age groups in the case of gulls: 1K ŽK, calendar year., 2K, 3K, 4K and adult, and four in the case of ringed seal: 0 year; 1]3-years-old; 4]6-years-old and G 7-years-old. Spatial trends have been analysed for each age group separately using a one-way ANOVA, followed by application of Tukey’s studentised range test. Lead concentrations in polar cod and glaucous gull were in many occasions below the detection limit. In these cases the evaluation of differences among two areas has been based on the distribution of the number of values below detection limit among areas. If the distribution of values below detection limit observed have an estimated probability below 5% with a H0 of equal distribution estimated by resampling simulations ŽSimon, 1995., the lead concentrations are concluded to be different among areas. Data from biota were all presented on wet weight basis Žwet wt... For recalculation into dry weight following mean dry weight percentages were: Blue mussel soft tissue: 17.6%; polar cod liver: 51.3%; shorthorn sculpin liver: 30.1%; glaucous gull liver: 30.8%; Iceland gull liver: 31.4% and ringed seal liver: 29.2%.

3. Results Element concentrations together with the basic statistics are given for each media and locality in Appendices A, B, C and D. In the following sections the data are presented with respect to dependency of covariate and to geographical trends. 3.1. Dependency of co¨ ariates Table 1 gives a summary of the covariate de-

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14 Table 1 Summary of covariate dependencies found in Greenland marine samples during AMAP phase 1a Covariate

Element:

Pb

Cd

Hg

Se

Sediment Blue mussel Polar cod Shorthorn sculpin Glaucous gull Iceland gull Ringed seal

Li Length Length Length Age Age Age

q q n.a. n.s. n.s. n.s n.s.

q q n.s. n.s. q q q

q q q q n.s. n.s. q

n.a. y n.s. n.s. q q q

a

Abbre¨ iations:H indicates increasing concentrations with the covariate; yindicates decreasing concentrations with the covariate; n.s. indicates no significant relationship or that area conflicting results were found; and n.a. indicates that no analysis was done.

pendencies found. They are presented for each element below. Lead, cadmium and mercury concentrations in sediments increased with increasing lithium concentrations and were, therefore, normalised to the average Li concentration, 22 mgrkg according to Loring and Rantala Ž1992.. For all elements the relationship between lithium and element concentrations did not differ significantly between localities. The lead concentration in soft tissues of blue mussel increased with increasing shell length. The relationship between shell length and lead concentration did not differ significantly between localities. Lead concentrations in polar cod were too low to allow for an analysis of length dependency. The lead concentration in shorthorn sculpin was also low, although not below the detection limit. In shorthorn sculpin the lead concentrations yielded conflicting results regarding length dependency. Hence, an increase of lead concentration with fish length was observed in fish from Nanortalik, whereas the opposite was found from the other localities. Lead concentrations in gull and ringed seal showed no dependency on age. In blue mussel, cadmium concentration increased with increasing shell length in the samples from Qeqertarsuaq and Uummannaq, while no such tendency was seen in the sample from

7

Nanortalik. Cadmium concentrations in liver of polar cod and shorthorn sculpin showed no significant dependency on fish length, whereas, cadmium in liver was clearly accumulated with age in gull and ringed seal. In blue mussel, the mercury concentration increased with increasing size. However, the relationship between shell length and mercury concentration differed between localities. In both polar cod and shorthorn sculpin, the liver mercury concentrations increased with increasing length of the fish. In both fish species the relationship between fish length and mercury concentrations did not differ significantly among localities. In the liver of gull, conflicting relationships between mercury concentrations and age were seen, whereas, in the liver of ringed seal the mercury concentration clearly increased with age. In blue mussel, the selenium concentration decreased with increasing shell length. However, this relationship differed significantly among localities. In polar cod, the selenium concentration was found to be independent of fish length. In shorthorn sculpin, the selenium concentration showed conflicting dependency of fish length, with an increasing tendency in two localities, and a decreasing tendency in two other areas. Selenium concentrations in liver of gulls and ringed seal increased with age. 3.2. Geographical trends In order to make geographical comparisons, the concentrations in sediments were normalised to the concentration of lithium, and those in animals to the same length or age in cases where covariates influenced element concentrations. The normalisation procedures used in each case depend on the results of the statistical analyses and are further described in the materials and methods section. An overview of the geographical comparisons is shown in Table 2. The geographical differences are presented for each element below. 3.2.1. Lead The highest mean Li-normalised lead concen-

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F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

trations in sediments were found in Nanortalik and Ittoqqortoormiit, and the lowest concentration was found in sediments from Avanersuaq. No significant difference in length normalised lead concentration was found in blue mussel from Uummannaq and Nanortalik, while the lowest concentration was found in blue mussel from Qeqertarsuaq. In polar cod from Avanersuaq only 3 specimens out of 24 had lead concentrations above the detection limit of 0.004 mgrg wet wt., whereas 23 out of 25 fish from Ittoqqortoormiit were above that detection limit. This distribution of numbers of values below detection limit was significantly different from an equal distribution

estimated by a resampling simulation, and it is therefore concluded that the lead concentration in polar cod was significantly higher in Ittoqqortoormiit than in Avanersuaq. The lead concentration in liver of shorthorn sculpin from Ittoqqortoomiit was also significantly higher than that found at the other localities. For gulls, the number of values below detection limit Ž0.009 mgrg wet wt.. was 1 in Ittoqqortoormiit, 10 in Nanortalik, 16 in Qeqertarsuaq and 24 in Avanersuaq. The conclusion based on results from resampling simulations was that glaucous gull from Ittoqqotoormiit had a significantly higher lead level when compared to gulls from the other three areas. The lead concentration in ringed seal did not show clear differences among localities. Ringed seal from Nanortalik did, however, show a lower mean lead concentration than those from Avanersuaq and Qeqertarsuaq. 3.2.2. Cadmium The highest mean Li- normalised cadmium

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

concentrations was found in sediments from Nanortalik and the lowest in Ittoqqortoormiit, however, only the two extremes were significantly different. In blue mussel the mean cadmium concentration was significantly higher in blue mussel from Qeqertarsuaq than in the two other areas. In polar cod the mean cadmium concentration was significantly higher in Avanersuaq than in Ittoqqortoormiit. Also in shorthorn sculpin the highest level of cadmium was found in fish from Avanersuaq, however, the level was only significantly different from that found in fish from Nanortalik. For all ages of glaucous gull the highest mean cadmium concentration was found in gulls from Nanortalik, however, this was only significantly higher than in gulls from Qeqertarsuaq in the case of age 1K, from Avanersuaq in the case of age 2K and higher than in gulls from Ittoqqortoormiit in the case of adults. Also for ringed seal a relative consistent geographical pattern between age groups was found. In seal liver from Qeqertarsuaq, the mean cadmium concentration was considerably higher for all age groups than in seal livers from the other localities. The differences between Qeqertarsuaq and the other areas were significant for all age groups except age group G 7, probably due to the low sample number and larger age range in this age group.

3.2.3. Mercury The mean Li-normalised mercury concentration in sediments was significantly highest in Nanortalik and significantly lowest in Avanersuaq. Blue mussel from Nanortalik had, likewise, significantly higher mean normalised mercury concentration than blue mussels from the two other areas, although the differences were small. No difference was found for polar cod from Avanersuaq and Ittoqqortoormiit, while in shorthorn sculpin mean normalised mercury concentrations were highest in Ittoqqorttoormiit and lowest in Nanortalik As for sediment and blue mussel the mean mercury concentration in 1K glaucous gull from Nanortalik was significantly higher than in gulls from Avanersuaq and Qeqertarsuaq, and in 2K glaucous gull from Nanortalik

9

significantly higher than in gulls from Avanersuaq. In adult glaucous gull mean mercury concentration was significantly highest in gulls from Ittoqqortoormiit and lowest in gulls from Nanortalik. In the liver of ringed seal significant differences between localities in mean mercury concentration were only found for age group 1]3 years, whilst ringed seal from Ittoqqortoormiit had significantly highest mean concentration and those from Avanersuaq significantly lowest. 3.2.4. Selenium The mean length normalised selenium concentration in blue mussel was significantly higher in Uummannaq when compared to the two other areas, although the differences were small. No significant difference was found in the mean selenium concentration of polar cod from Avanersuaq and Ittoqqortoormiit. In shorthorn sculpin on the other hand, the mean selenium concentration was found to be significantly highest in fish from Avanersuaq. The mean selenium concentrations in glaucous gull from Avanersuaq were likewise highest for all ages, but only significantly so for age 1K. The significant lowest levels were found for age 1K and adults in glaucous gull from Qeqertarsuaq. There were no clear differences in the mean selenium concentration in seal liver between localities. The only significant differences found was in age group 1]3 years, where seals from Ittoqqortoomiit and Nanortalik had higher selenium levels when compared to seals from Qeqertarsuaq and Avanersuaq.

4. Discussion 4.1. Dependency of co¨ ariates Lead concentrations in blue mussel were found to increase with the shell length, which is in accordance with earlier findings Že.g. Popham and D’Auria, 1983; Riget et al., 1996.. The influence of length in case of shorthorn sculpin showed conflicting results as Johansen et al. Ž1998. have reported a decrease in lead concentrations in

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F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

liver with increasing fish length. There is no indication that lead accumulates with age in the liver of either gulls or ringed seal. A lack of correlation between tissue lead concentrations and age has been found in a large number of Arctic marine mammals including narwhals, belugas, pilot whales, white beaked dolphins and polar bears ŽWagemann et al., 1983, 1990; Muir et al., 1988; Norheim et al., 1992.. The increasing of cadmium concentration with size of blue mussels and fish length were in accordance with previous findings Že.g. Bohn and Fallis, 1978; Riget et al., 1996, 1997.. Cadmium concentrations in liver have also been reported to increase with age in gull and ringed seal from Greenland ŽNielsen and Dietz, 1989; Dietz et al., 1998b.. In general, mercury concentrations were found to increase in biota with sizerage of blue mussels, fish, and seals from Greenland in accordance with previous findings Že.g. Riget et al., 1996, 1997; Dietz et al., 1998b.. For gulls, no significant relationship between mercury concentrations and age was found, in accordance with studies by Nielsen and Dietz Ž1989. and Nicholson Ž1981.. In other Greenlandic animal groups, such as whales ŽHansen et al., 1990; Palulan-Muller et al., 1993. and ¨ polar bears ŽUrsus maritimus. ŽDietz et al., 1995. mercury concentrations have previously been found to increase with age. A decreasing trend in selenium concentrations in blue mussel with increasing shell length has been reported previously by Riget et al. Ž1996.. The relationship between selenium concentration and length observed in polar cod and shorthorn sculpin in this study were conflicting. A decrease in selenium concentrations with increasing fish length has previously been observed in a number of fish species from Greenland ŽRiget et al., 1997.. Selenium concentrations in liver of gulls and ringed seal increased with age. No studies of selenium accumulation in seabirds from Greenland have been carried out prior to this study. In the case of marine mammals, Dietz et al. Ž1998b. also found significant positive correlations with age in liver of ringed seal. This has also been documented for other animal groups from Greenland, such as whales ŽHansen et al., 1990; Palu-

lan-Muller et al., 1993. and polar bears ŽDietz et ¨ . al., 1995 . 4.2. Le¨ els and geographical trends 4.2.1. Lead Lead levels found in marine biota and sediments in this study were within the range of levels observed previously ŽDietz et al., 1996.. Concentrations in fish, birds and seals were generally low, and in several cases close to or lower than the detection limit of the analytical techniques used. The highest lead levels in most cases were found in Ittoqqortoormiit, and in several cases the lowest levels in Avanersuaq ŽTable 2.. Levels in the two other areas ŽQeqertarsuaq and Nanortalik. were intermediate in most cases. This is in accordance with previous findings, as Dietz et al. Ž1996. reported higher lead concentrations in east than in west Greenland in ringed seal and a bivalve Žgreen crenella Ž Musculus discors... 4.2.2. Cadmium The levels of cadmium found in marine biota and sediments in this study were within the range of levels observed previously, and in general cadmium levels in Greenland biota must be considered high ŽDietz et al., 1996.. No consistent geographical pattern for cadmium levels was evident between species. Cadmium levels in liver of fish from north Greenland were higher compared to other regions, which is in accordance with the geographical pattern reported by Riget et al. Ž1997.. Ringed seals at Qeqertarsuaq had higher levels than the other regions to the north, south and east. This is not in agreement with an earlier study, in which the highest cadmium concentrations in ringed seal were found in the northern region ŽDietz et al., 1998b.. However, ringed seals from Qeqertarsuaq were not included in that study, which may explain the differences. But blue mussels also had the highest cadmium levels in Qeqertarsuaq. The cause of the high cadmium levels around Qeqertarsuaq remains unknown as yet. 4.2.3. Mercury The mercury levels observed in Greenlandic

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

sediment and the relatively high levels in biota were within the range of those reported previously. No consistent geographical pattern for mercury levels was evident between species. There is, however, a tendency for the highest concentrations to be found in east Greenland Žshorthorn sculpin, polar cod, adult gulls. ŽTable 2.. This was also found in earlier studies of seabirds ŽNielsen and Dietz, 1989. and ringed seal ŽDietz et al., 1998b., whereas a different pattern was observed for shorthorn sculpin ŽRiget et al., 1997..

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tent geographical pattern between selenium concentrations in the species analysed is apparent ŽTable 2.. This is not in agreement with an earlier study, which showed that selenium levels in almost all cases were higher in north-west Greenland than in other Greenland regions ŽDietz et al., 1996..

Acknowledgements The authors wish to thank the hunters and colleagues having participated in the collection of material and the laboratory technicians for their work on the metal analyses. We extend our thanks to Mark White for improving the linguistics of the manuscript. Furthermore, we thank the Danish Environmental Pollution Agency for funding.

4.2.4. Selenium The selenium levels found in Greenland biota were within the range of those observed previously, and are generally high ŽDietz et al., 1996.. Concentrations did not differ as much between study areas as for the other elements. No consis-

Appendix A. a Lead, concentration in sediments and biota collected in Greenland in 1994–1995 Lead Matrix Species, tissue Age group Sedimentsb Blue mussels, soft tissuec Polar cod, liver Shorthorn sculpin, liver Glaucous gull, liver all ages Iceland gull, liver all ages Ringed seal, liver all ages a

Avanersuaq N

5

GM

9.75

R.S.E.

Uummannaq

Qeqertarsuaq

N

GM

R.S.E.

N

14

0.145

1.07

5 15

1.17

Nanortalik

Ittoqqortoormiit

R.S.E.

N

GM

R.S.E.

13.7 0.088

1.05 1.07

5 15

16.8 0.138

1.05 1.06

1.35

25

0.008

1.34

25 25

0.008 0.022

1.45 1.28

22

0.38

1.21

27

0.017

1.16

GM

24 25

- 0.004 0.004

] 1.30

25

0.005

25

- 0.009

]

19

- 0.009

]

17

0.015

1.23

6

- 0.009

]

8

0.016

1.38

38

0.019

25

0.011

1.13

25

0.022

1.21

1.09

N

GM

R.S.E.

6

16.1

1.05

Abbre¨ iations: GM, geometric mean; R.S.E.s relative standard error, i.e. the antilogarithm of the standard error of concentrations on logarithmic scale. All concentrations are given in mgrg wet weight except sediment which are presented as mgrg dry weight. b Normalised to Li concentrations of 22 mgrg d.w. c Normalised to shell length of 5.2 cm.

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

12

Appendix B. Cadmium concentration in sediments and biota collected in Greenland in 1994–1995 Cda Matrix Species, tissue Age group Sedimentsb Blue mussels, soft tissuec Polar cod, liver Shorthorn sculpin, liver Glaucous gull, liver 1K 2K 3K 4K Adult Iceland gull, liver 1K 2K Adult Ringed seal, liver Age group 0 years Age group 1]3 years Age group 4]6 years Age group G 7 years

Avanersuaq N

5

GM

0.136

R.S.E.

Uummannaq

Qeqertarsuaq

Nanortalik

N

GM

R.S.E.

N

R.S.E.

N

GM

R.S.E.

14

0.577

1.05

5 15

0.160 0.820

1.21 1.05

5 15

0.192 0.609

1.03 1.04

1.33

GM

Ittoqqortoormiit

24 25

0.650 1.40

1.12 1.19

25

1.35

1.14

25

0.505

1.08

17 2

0.290 0.301

1.10 1.28

7 1

0.145 4.23

1.58 ]

2 11 1

0.726 2.74 5.70

1.70 1.27 ]

6

8.38

1.43

12

9.05

1.21

3

6

0.278

1.34

2 1 5

0.400 0.649 2.61

1.05 ] 1.54

12.2

1.23

N

0.096

1.16

25 25

0.303 1.01

1.07 1.16

2 22

2.26 1.59

3.25 1.18

1

0.062

]

10

4.07

1.42

8.44

1.13

0.612

1.77

5

13.2

1.15

1

3.35

]

4

0.452

2.2 6

21

17.9

1.08

24

2.92

1.13

7

7.90

1.49

9

23.1

1.14

11

1.68

2

23.7

1.54

5

11.0

R.S.E.

6

7

7

GM

14.2

1.36

a Abbre¨ iations: GM, geometric mean; R.S.E.s relative standard error, i.e. the antilogarithm of the standard error of concentrations on logarithmic scale. All concentrations are given in mgrg wet weight except sediment which are presented as mgrg dry weight. b Normalised to Li concentrations of 22 mgrg d.w. c Normalised to shell length of 5.2 cm.

Appendix C. Mercury concentration in sediments and biota collected in Greenland in 1994–1995 Hg a Matrix Species, tissue Age group Sedimentsb Blue mussels, soft tissuec Polar cod, liverd Shorthorn sculpin, livere Glaucous gull, liver 1K 2K 3K 4K Adult

Avanersuaq N

4

Uummannaq

GM

R.S.E.

0.0045

1.89

Qeqertarsuaq

Nanortalik

Ittoqqortoormiit

N

GM

R.S.E.

N

GM

R.S.E.

N

GM

R.S.E.

14

0.0149

1.02

5 15

0.018 0.0146

1.28 1.03

5 15

0.033 0.0167

1.12 1.02

24 25

0.011 0.0392

1.08 1.10

25

0.0198

1.10

25

0.0102

1.10

17 2

0.542 0.462

1.10 1.03

7 1

0.461 0.875

1.33 ]

2 11 1

2.77 1.90 1.37

1.17 1.11 ]

6

1.75

1.31

12

0.171

1.24

3

1.68

1.19

N

GM

R.S.E.

6

0.016

1.11

25 25

0.013 0.0682

1.08 1.10

2 22

3.39 2.40

1.72 1.07

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

13

Appendix C. Ž Continued. Matrix Species, tissue Age group Iceland gull, liver 1K 2K Adult Ringed seal, liver Age group 0 years Age group 1]3 years Age group 4]6 years Age group

Avanersuaq N

GM

R.S.E.

Uummannaq

Qeqertarsuaq

N

N

GM

R.S.E.

Nanortalik

GM

R.S.E.

6

0.238

1.10

N

Ittoqqortoormiit

GM

R.S.E.

2 1 5

0.307 0.603 0.456

1.03 ] 1.51

7

0.562

1.32

5

0.930

1.16

1

0.700

]

4

0.533

1.25

21

1.38

1.12

24

1.53

1.11

7

6.66

1.24

9

3.55

7

6.45

1.34

2

4.72

N

GM

R.S.E.

1

0.357

]

10

3.51

1.18

1.27

11

5.09

1.18

1.49

5

11.9

1.50

G 7 years a Abbre¨ iations: GM, geometric mean; R.S.E.s relative standard error, i.e. the antilogarithm of the standard error of concentrations on logarithmic scale. All concentrations are given in m grg wet weight except sediment which are presented as m grg dry weight. b Normalised to Li concentrations of 22 m grg d.w., one outlayer from Avanersuaq removed. c Normalised to shell length of 5.2 cm. d Normalised to length of 23 cm. e Normalised to length of 24.3 cm.

Appendix D. Selenium concentration in sediments and biota collected in Greenland in 1994–1995 Se a Matrix Species, tissue Age group Blue mussels, soft tissueb Polar cod, liver Shorthorn sculpin, liver Glaucous gull, liver 1K 2K 3K 4K Adult Iceland gull, liver 1K 2K Adult Ringed seal, liver Age group 0 years Age group 1]3 years Age group 4]6 years Age group G 7 years a

Avanersuaq N

GM

Uummannaq R.S.E.

Qeqertarsuaq

Nanortalik

Ittoqqortoormiit

N

GM

R.S.E.

N

GM

R.S.E.

N

GM

R.S.E.

14

1.03

1.03

15

0.843

1.03

15

0.810

1.02

24 25

0.724 1.08

1.03 1.05

25

0.986

1.03

25

0.925

1.03

17 2

2.75 3.31

1.11 1.37

7 1

1.05 1.44

1.11 ]

2 11 1

1.90 1.44 2.86

1.18 1.12 ]

6

4.99

1.41

12

1.33

1.09

3

3.05

1.44

6

0.772

1.05

2 1 5

1.33 1.70 2.37

1.17 ] 1.26

N

GM

R.S.E.

25 25

0.725 0.871

1.07 1.05

2

3.98

2.04

22

3.35

1.22

1

1.03

]

10

2.17

1.14

7

1.00

1.17

5

1.92

1.60

1

1.18

]

4

0.932

1.10

21

1.30

1.07

24

2.03

1.07

7

3.65

1.18

9

2.29

1.19

11

2.93

1.12

7

3.94

1.21

2

4.56

1.12

5

4.13

1.17

Abbre¨ iations: GM, geometric mean; R.S.E.s relative standard error, i.e. the antilogarithm of the standard error of concentrations on logarithmic scale. All concentrations are given in m grg wet weight except sediment which are presented as m grg dry weight. b Normalised to shell length of 5.2 cm.

14

F. Riget et al. r The Science of the Total En¨ ironment 245 (2000) 3]14

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