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Article

Organic Pollution in Surface Waters from the Fuglebekken Basin in Svalbard, Norwegian Arctic

by
Żaneta Polkowska
1,*,
Katarzyna Cichała-Kamrowska
1,
Marek Ruman
2,
Krystyna Kozioł
3,
Wiesława Ewa Krawczyk
2 and
Jacek Namieśnik
1
1
Department of Analytical Chemistry, The Chemical Faculty, Gdansk University of Technology, 11/12 Narutowicza St., Gdansk 80-233, Poland
2
Faculty of Earth Sciences, University of Silesia, 60 Będzińska St., Sosnowiec 41-200, Poland
3
Department of Geography, University of Sheffield, Winter Street, Sheffield S10 2TN, UK
*
Author to whom correspondence should be addressed.
Sensors 2011, 11(9), 8910-8929; https://doi.org/10.3390/s110908910
Submission received: 8 August 2011 / Revised: 4 September 2011 / Accepted: 8 September 2011 / Published: 15 September 2011
(This article belongs to the Special Issue Sensing of Organic Pollution in Soil, Air, Water and Food)
Browse Figures
Versions Notes

Abstract

: The Fuglebekken basin is situated in the southern part of the island of Spitsbergen (Norwegian Arctic), on the Hornsund fjord (Wedel Jarlsberg Land). Surface water was collected from 24 tributaries (B1–B24) and from the main stream water in the Fuglebekken basin (25) between 10 July 2009 and 30 July 2009. The present investigation reveals the results of the analysis of these samples for their PAH and PCB content. Twelve of 16 PAHs and seven PCBs were determined in the surface waters from 24 tributaries and the main stream. Total PAH and PCB concentrations in the surface waters ranged from 4 to 600 ng/L and from 2 to 400 ng/L respectively. The highest concentrations of an individual PCB (138–308 ng/L and 123 ng/L) were found in samples from tributaries B9 and B5. The presence in the basin (thousands of kilometres distant from industrial centres) of PAHs and PCBs is testimony to the fact that these compounds are transported over vast distances with air masses and deposited in regions devoid of any human pressure.

1. Introduction

The contamination of the aquatic environment by stable organic compounds like polycyclic aromatic hydrocarbons (PAHs) or polychlorinated biphenyls (PCBs) is giving cause for alarm worldwide [1,2]. Because of their properties, these compounds can not only occur in water; they can be deposited in sediments or accumulate in the tissues of aquatic animals and can also be metabolized to compounds that are even more toxic and/or carcinogenic [2,3]. PAHs may turn up in the aquatic environment as a result of natural events—forest fires, volcanic eruptions, natural leakage, diagenesis of organic matter, synthesis by plants; but their presence there may also be anthropogenic: petrogenic (emergencies and leakage from the extraction and processing of crude oil and its products) and combustion (incomplete combustion at high temperatures and pyrolysis of organic matter) [4–6]. On the other hand, the presence of PCBs is solely due to human agencies. Although the production of PCBs has ceased in many countries, they may still be present in the environment. PCBs are emitted from anthropogenic sources, such as historical intentional production, utilization, disposal and accidental releases of products or materials containing these compounds. The incidental or unwanted formation of PCBs, e.g., de novo synthesis in combustion processes, thermal process of chlorine-containing materials or combustion of by-products, such as fuel combustion, waste incineration, the oxidation of iron, spills, accidents and emergencies should be also treated as a possible environmental threat [1,7–12]. The issue of the transport and fate of PAHs and PCBs substances in remote areas has received increasing attention during the past decade. Long-range atmospheric transport, deposition and air/water exchange are key processes governing the distribution of PAHs and PCBs on a global scale [2]. PAH and PCB pollutants enter the surface waters, as a result of wet and dry deposition, and via runoff from area sources (industry, households).

The Arctic, regarded in the past as a pristine area in terms of anthropogenic pollution, has nowadays become an area of great concern. Previous studies have demonstrated that this region is a significant recipient of various groups of persistent toxic substances originating from countries in both the Northern and Southern Hemispheres [2]. In the Arctic PAHs have been detected and determined in samples from the abiotic environment: snowpit (Greenland) [13,14], lake sediments (Svalbard) [2,15] and sea sediments (Barents Sea) [16]. PCBs have been determined far more frequently in samples from the Arctic, e.g., in lake sediments (Svalbard, Bjørnøya, Canadian Arctic, Russia, Greenland) [2,15,17–22]. PAHs have been determined in various tissues and organs from wildlife (Svalbard, Bjørnøya, Hornøya, Barents Sea, Franz Josef Land, Jan Mayen, Vestfjorden, Lofoten, Greenland, North Sea) [16,17,23–25].

PAHs and PCBs are highly toxic and are included in the priority substance list of the Water Framework Directive. Although more than half of PAH compounds are not carcinogenic, distribution of PAHs and PCBs in the environment as well as the associated potential health risks have become the focus of much attention. Their presence in Svalbard surface waters in combination with other potentially toxic compounds could have deleterious effects, which is why defining the source of origin of these contaminants in the environment is a matter of urgency.

In respect to the discussion of the PAHs one needs to emphasize that more than half of them shown are non-carcinogenic, and that the same applies to their gas phase/particulate phase ratio: naphthalene, phenanthrene, anthracene, acenaphth(yl)ene are fully in the gas phase and not associated with the particulate phase (dust); this starts with fluoranthene.

The Fuglebekken basin is situated in the southern part of the island of Spitsbergen, on the Hornsund fjord (Wedel Jarlsberg Land). It has an area of ca. 2–3 km2. It includes the steep slopes of the Ariekammen and Fugleberget, as well as a large part of the Fuglebergsletta plain together with the raised beach. The highest point of the basin lies at 568.7 m above sea level, whereas the lowest lies at sea level (the average height is 284.35 m). Gradients in the basin are very steep (400.49‰). In the upper part of the basin there are several streams, which join into one at the point where it crosses the berm—this is where the water level recorder was installed. One of the tributaries drains a small lake that formed behind the berm. Below the measurement station, the stream takes the form of an anastomosing river. The Fuglebekken main stream debouches into the Isbjörnhamna, cutting across the stony beach. In dry periods, the outflow may be completely concealed beneath boulders. The hydrologically active part of the year in the Fuglebekken lasts for 145 days. Pulina et al. [26] describe the hydrological season in the Fuglebekken, dividing it into three periods: snowmelt and rapid outflow (until mid-July), medium and small flows strictly due to precipitation, and the autumn-winter period of large flows due to intensive precipitation. Hydrological measurements made in the Fuglebekken during an expedition in 1979–1980 indicated a mean flow in the stream (excluding periods when no water flowed) of 0.082 m3·s−1. The outflow at this time was 822.2 mm, which was 95% of the total precipitation (864.5 mm; Pulina et al. [27]). The shape and location of this basin make it a very interesting object of study. The presence in this basin (thousands of kilometres distant from industrial installations) of PAHs and PCBs provide evidence for their having been transported over vast distances with air masses and their deposition in areas wholly devoid of any pressure from human agencies.

2. Experimental Section

2.1. Sampling and Site Description

Surface water was collected from 24 tributaries (B1–B24) and from the main stream in the Fuglebekken basin (25). Location map for the sampling area (Fuglebekken basin, marked with black frame). Major settlements in Svalbard and Polish Polar Station in Hornsund (labelled ‘Hornsund’ are shown on Figure 1. The details of the sampling locations are given in Table 1.

The main stream water (Fuglebekken) was sampled between 10 July 2009 and 14 September 2009; tributaries B1–B24 were sampled on 30 July 2009. The Fuglebekken has an area of 2.02 km2 (real surface area 2.64 km2). Geologically the basin belongs to the Hecla Hoek formation, composed of metamorphic rocks; those within the basin were formed during the Proterozoic (Hjelle [28]). The basin consists entirely of rocks of the Ariekammen group of the Isbjörnhamna formation.

According to Pękala [29], every year some 340–580 g of weathered rock material comes away from every m2 of the surface of the nunataks north of Hornsund. There are extensive alluvial fans at the base of the slopes in the northern part of the basin. The remaining, flat part is a raised beach. In places structural soils have formed on its surface in the form of rocky rings (in the NE). The former berm, of marine pebbles, also crosses the basin. The western watershed of the Fuglebekken consists of low rocks, morphologically interpreted as roches moutonées. To the east the basin borders on the lateral moraine of the Hans Glacier, embracing the outwash plain on a rocky substrate. The total length of the watershed is 6.3 km, and its mean slope is 90.27‰.

The basin’s morphology can be characterized by means of shape indices. With a length of 2.1 km and an average width of 0.96 km, the form factor is 0.45. Table 2 lists the parameters of the Fuglebekken river basin in detail.

The area adjacent to the basin is where the meteorological station operated by the Polish Polar Station is situated. The mean annual temperature there in 1978–2006 was −4.4 °C. The maximum mean monthly temperature occurs in July (4.4 °C), the minimum in January (−11.2 °C). In 1979–2006 the mean annual precipitation was 430 mm, and the snow cover (av. depth 20 cm) lasted from an average of 241 days in the year.

2.2. Chemicals

All solvents used for sample processing and analyses were GC-pure quality and were purchased from the Sigma-Aldrich Company (dichloromethane-PESTANAL®, solvent for residue analysis; methanol-CHROMASOLV®, for HPLC, ≥99.9%; hexane-CHROMASOLV®, for HPLC, ≥97.0% (GC)). A mixture of 16 PAHs and two deuterated internal standards (naphthalene-d8, benzo(a)anthracene-d12) in dichloromethane at a concentration of 2,000 μg/mL for each were from Restek Corporation (USA) and Supelco (USA) respectively. A working stock solution was prepared from seven selected PCB standards (IUPAC Nos. 28, 52, 101, 118, 153, 138 and 180). Standards were also purchased from Restek Corporation (USA) as 10 μg/mL solutions in isooctane. Certified standards of 13C-labelled PCB 28 and PCB 180 (40 μg/mL in nonane) were obtained from Cambridge Isotope Laboratories (USA) [30,31].

2.3. Analytical Procedure

A 1 L sample of water was extracted with 30 mL dichloromethane, two deuterated internal standards (naphthalene-d8 (m/z 136) and benzo(a)anthracene-d12 (m/z 240)), and two isotopically labelled internal standards of PCB 28 (m/z 270, 268) and PCB 180 (m/z 408, 406) and shaken for 20–30 min. After liquid-liquid extraction (LLE), the extract was evaporated to a volume of 300 μL under a gentle stream of nitrogen (Figure 2) [30–34].

The final extracts were analysed using an Agilent Technologies 7890A gas chromatograph with an Agilent Technologies 5975C mass spectrometric detector and split/splitless injector (7683B). A ZB-5MS capillary column (5% phenyl + 95% dimethylpolysiloxane, 30 m × 0.25 mm × 0.25 μm) was used. The temperature programme was the following: initial temperature 40 °C, 40 °C to 120 °C at 40 °C min−1, then 120 °C up to 280 °C at 5 °C min−1 where it was held for 17 min (PAHs) and for 5 min (PCBs). The carrier gas was helium with inlet pressure 70 kPa. The injection volume selected for all analyses was 2 μL. The mass spectrometer was operated in the selected ion monitoring (SIM) mode. The following ions were monitored: (m/z) PAH: 128, 127, 152, 151, 154,153, 166, 165, 178, 176, 203, 202, 228, 226, 252, 250, 277, 276, 279 and 278, and PCB: 258, 256, 292, 290, 328, 326, 362, 360, 396, and 394 [35,36]. Before sample analysis, the relevant standards were analysed to check column performance, peak height and resolution, and the limits of detection and quantification. A solvent blank, a standard mixture and a procedural blank were run in each sequence of samples to check for contamination, peak identification and quantification. Compounds were identified mainly by their retention times. Measuring range, detection and quantification limits are presented in Table 3.

3. Results and Discussion

3.1. Levels of PAHs in Surface Waters and an Indication of Their Origin

The concentrations of 12 of 16 PAHs in surface water from 24 tributaries and stream water (Fuglebekken) are shown in Table 4. These compounds were determined at 17 of the 25 surface water sampling points, at concentrations ranging from 4 to 600 ng/L. The highest concentration of an individual PAH (naphthalene, 557 ng/L) was found in a sample from tributary B5.

Points B5, B6 and B7, where decidedly higher PAH levels were detected and determined in the samples, lie at the foot of a mountain down which meltwater from snow and ice flows. These waters flush out pollutants from the air and also from the mountainsides, where on days without precipitation contaminants are deposited that arrived there with dusts. These contaminants are then carried by the tributaries to the Fuglebekken main stream. In those parts of the basin farthest away from the mountain range PAH levels were much lower as a result of their having been diluted with cleaner stream water. Moreover, points B5–B7 are situated in erosion hollows (gullies), where snow accumulates and lies.

The spatial distribution of PAH concentrations showed considerable variation within the study area, and there were clear differences in residue levels between sampling points. Samples from points B1–B4, at the edge of the basin, contained very different levels of naphthalene, where these values were well below 1 ng/L. In samples taken elsewhere in the basin naphthalene levels were from a few to several hundred ng/L, whereas acenaphthylene, anthracene and fluorene were found more frequently at those points.

The occurrence of high PAH levels in these areas might be due to their proximity to a coal mine. Mining and excavation activities took place at this site for a long time; the excavated products were transported by train from the mine site to a dock, and some of the coal was used to run a power station. Although the mining operation was closed in 1962, railways and coal heaps remain in the area and could be contributing to the elevated levels of PAHs in the Fuglebekken.

To date, no analysis of surface water samples from Svalbard for the presence of PAHs has been carried out. Even so, the compounds have been detected in bottom sediments in Ny-Ålesund, Wijdefjorden and Adventfjorden [2,16,18], and also in ambient particulate matter [15], surface soil [17], moss [17] and reindeer dung [17]. PAHs have also been detected and determined in bivalves samples from Svalbard [16] (Table 5). The PAH most commonly determined in bottom sediments on Svalbard was naphthalene [2], just as in the water samples from the Fuglebekken.

The highest PAH level measured in the 1995 survey (191 ng/g dry wt) was found in sediment from Tenndammen, which is affected by coal combustion and the diesel power plants in Longyearbyen (Svalbard). Together with the recent upsurge in research activities and the establishment of research stations, the number of cruises and ships to Ny-Ålesund increased remarkably during 1996–2005. Total diesel fuel and petrol consumption by power stations and vehicles also increased slightly from 2001 to 2005. Consumption of diesel in the power stations in 2001 and 2005 was 1,009 and 1,130 m3 respectively, and that of vehicle fuels was 34 m3 in 2001 and 37 m3 in 2005 [2].

Trends in the intensity of PAH deposition, evaluated from cores taken from the Arctic ice cap, have shown a dramatic increase in concentrations over the last 100 years that correlate well with the historical record of world petroleum production. An increase in the concentration of PAHs relative to those of fatty acids of terrestrial higher plant origin (C20–C32) demonstrated that contributions of anthropogenic PAHs have increased significantly since the 1930s. Similarly, other researchers have concluded from analyses of surface snow samples, also taken from the Arctic ice cap, that current PAH contamination is essentially due to fossil fuel combustion with some input from biomass burning [23].

PAHs are present in the Arctic environment from both anthropogenic and natural sources (petrogenic/biogenic). The literature makes reference to various methods of identifying sources of PAH emissions that are based on concentration ratios of particular compounds, for example, the ratio of a substituted compound to an unsubstituted one [12,35,37]. Petrogenic PAHs are formed slowly, over a long time, at moderate temperatures (100–300 °C), and are associated with fossil fuels (petroleum and coal). Combustion PAHs are formed during rapid, high-temperature combustion (>700 °C) of motor (automobile), bunker (shipping), and power plant (coals and petroleum) fuels. Combustion PAHs are also formed at the intermediate temperatures (400−600 °C) reached in the processing of coals into coal tars and coal tar products (e.g., creosote, or the coal tar pitch used in aluminium smelters). Thus, the characteristic PAH compositional profile of these different sources can be used to help distinguish them [36].

To further assess the potential sources of PAHs to the surface waters from Svalbard, PAH indicator ratios, commonly used to trace the origin of PAHs, were considered [35,37]. Several PAH indicator ratios in surface water sediments were compared to those in some typical sources reported in the literature (Table 6).

Phenanthrene/anthracene, the most commonly used ratio, ranged from 0.001 to 0.908 (mean 0.7) in surface water, which may suggest that the majority of PAHs determined in samples of water taken in various places in the Fuglebekken was derived from combustion sources. This is the same ratio as for lake sediments in Svalbard, which may suggest that the majority of PAHs in the lakes were derived from the same sources. On the other hand, although the number of samples was limited, the PAH ratios of coastal marine sediments (Svalbard) suggest petrogenic origins [2].

Relatively high fluoranthene/(fluoranthene + pyrene) ratios are also typical of aerosols associated with combustion PAHs [2,23]. The ratio characteristic of samples of water from the Fuglebekken indicate that PAHs probably originate both from local sources due to the burning of fossil fuels and high temperature biomass combustion, as well as from aerosol inputs through long-range atmospheric transport.

Table 7 sets out information that may be of help in interpreting the measurement data (Table 6). It shows that most of the contamination comes from the combustion source: for the samples from the tributaries (B1–B24), 99% is due to combustion and 1% to petrogenic influence. The situation regarding stream water is very similar. More than 70% of the samples are of combustion origin; the remainder is the result of petrogenic influence.

3.2. Levels of PCBs in Surface Waters and an Indication of Their Origin

The concentrations of 7 PCBs in samples of surface water from 24 tributaries and stream water (Fuglebekken) are shown in Table 8. These compounds were determined in samples taken from 20 of the 25 sampling points. Total PCB concentrations in surface water ranged from 2 to 400 ng/L. The highest concentrations of an individual PCB 138 (308 ng/L and 123 ng/L) were found in samples from tributaries B9 and B5. At these points the levels of PCB 101 and 118 were also high.

As far as PCBs are concerned, there are no data in the literature on markers that could indicate the sources of their emission. This is primarily because PCBs are synthesized chemically, so that in the environment they occur mainly as mixtures containing various amounts of their congeners. Hence, it is not possible to determine their points of origin on the basis of molecular ratios. Nevertheless, if we have data on PAHs at our disposal, by drawing comparisons and seeking mutual correlations we can “define” the probable source of emission of PCB compounds [36].

3.3. Loads of Organic Compounds Transported by the Fuglebekken Stream

The levels of organic pollutants in the Fuglebekken varied: in proportion to the volume of water carrier by each tributary of the basin’s main stream, these levels reflect the overall load of PAHs and PCBs that it carries into the Hornsund fjord. Table 10 lists the loads of PCBs and PAHs transported in the Fuglebekken basin.

The total load of PCBs present at the outlet of the Fuglebekken ranged from 0.06 mg per 24 h in the case of PCB-52 to 0.60 mg per 24 h in the case of PCB-118. The largest PCB loads in the main stream were recorded for the pentachlorobiphenyls PCB-101 and PCB-118. These two compounds made up to 6.4% of the total PCB load in the Fugle stream, while the measured congeners encompassed 14% of the total PCB load. The overall PCB load carried in 24 h is 17.9 mg, which is equivalent to the transport of 745 μg PCBs across the stream’s cross-section in 1 h. The load of PAHs in the Fuglebekken is half as great (9.90 mg per 24 h, 420 μg per h). The significant compounds among the PAHs were naphthalene, acenaphthylene and pyrene (0.89, 0.44 and 0.31 mg per 24 h respectively).

4. Conclusions

PAHs and PSBs were detected and determined in the waters of the Fuglebekken basin in Svalbard, Norwegian Arctic. In the case of PAHs it is easy to pinpoint the source on the basis of the concentration ratios of the relevant compounds. The presence of PAHs in Svalbard may be due to long-distance transport, and also to the combustion of fuel for transportation, heating and electric power production purposes at the Polish Polar Station. In the case of long-distance transport, taiga fires are also a probable source, as PAHs are also produced during the combustion of biomass. It takes just a few days for pollutants from Europe to reach the Arctic, and within a few weeks the toxins may have entered the food chain. Contaminants are transported much more slowly in sea water, carried as they are by sea currents: it is thought that it takes 30−40 years for contaminants to reach the Arctic by this means. Because of their lipophilic properties, PAHs are more commonly found in soils and sediments [2,18] than in waters. It is therefore likely that the PAH levels in the soils of the Fuglebekken basin are higher than those measured in the stream water. PAH levels in waters may also be affected by the rock load they are carrying and by dry atmospheric deposition. These compounds get into the basin mostly with precipitation, usually snow, which often lies for very long periods among the mountain peaks. Here, PAHs can be deposited together with dust that has been carried even for thousands of kilometres. Contaminants are transported to and within the Arctic along various routes. A major pathway is the atmospheric transport of contaminants from mid-latitudes to the Arctic region. In winter, areas of high pressure are present over the continents and of low pressure over the northern Pacific and Atlantic Oceans; the intense Siberian high-pressure cell tends to force air on its western side northwards into the Arctic. Consequently, airborne pollutants are transported from sources in Eurasia into the Arctic. In summer, the Eurasian flow is reversed, resulting in a weak north to south transport [65].

In contrast, the source of PCBs cannot be determined with any certainty. Given the current state of knowledge, however, it is possible, if we have levels of both PAHs and PCBs, to draw indirect inferences regarding the source of these latter compounds in the environment; this is also possible by comparing or seeking suitable correlations between PAH and PCB levels, and on the basis of information obtained from hydrological, meteorological and historical sources. PCBs may be present in Svalbard surface waters as a result of the long-range transport of air masses: the well known Arctic haze—a manifestation of the accumulation of atmospheric pollutants in the Arctic—is due to the minimal exchange of air with non-polar areas in winter. In the past these compounds were used in electrical equipment such as transformers, condensers and switches. The fact that such equipment was used at the Polish Polar Station could have led to the contamination of the running waters in the vicinity, especially if the reservoir from which these substances are released is the soil, however the results of recent studies indicate that levels of PCBs in the tissues of sea birds in the Arctic are falling, a trend that is expected to continue. Even so, PCBs, whose environmental content is decreasing only very slowly, continue to be the most serious pollutants of the Arctic.

Acknowledgments

The authors would like to thank the staff of the Polish Polar Station at Hornsund for the opportunity to carry out sampling and for their assistance with this work. This work was financially supported from the Project: The influence of polluting gases and dusts on the chemical composition of atmospheric precipitation and climate change in the Arctic and Antarctic (IPY/21/2007).

References

  1. Breivik, K; Sweetman, A; Pacyna, J; Jones, K. Towards a global historical emission inventory for selected PCB congeners—A mass balance approach: 2. Emissions. Sci. Total Environ 2002, 290, 199–224. [Google Scholar]
  2. Jiao, L; Zheng, GJ; Minh, TB; Richardson, B; Chen, L; Zhang, Y; Yeung, LW; Lam, JCW; Yang, X; Lam, PKS; Wong, MH. Persistent toxic substances in remote lake and coastal sediments from Svalbard, Norwegian Arctic: Levels, sources and fluxes. Environ. Pollut 2009, 157, 1342–1351. [Google Scholar]
  3. Dickhut, RM; Canuel, EA; Gustafson, KE; Liu, K; Arzayus, KM; Walker, SE; Edgecombe, G; Gaylor, MO; Macdonald, EH. Automotive sources of carcinogenic polycyclic aromatic hydrocarbons associated with particulate matter in the Chesapeake Bay region. Environ. Sci. Technol 2000, 34, 4635–4640. [Google Scholar]
  4. Xu, J; Yu, Y; Wang, P; Guo, W; Dai, S; Sun, H. Polycyclic aromatic hydrocarbons in the surface sediments from the Yellow River, China. Chemosphere 2007, 67, 1408–1414. [Google Scholar]
  5. He, F; Zhang, Z; Wan, Y; Lu, S; Wang, L; Bu, Q. Polycyclic aromatic hydrocarbons in soils of the Beijing and Tianjin regions: Vertical distribution, correlation with TOC and transport mechanism. J. Environ. Sci 2009, 21, 675–685. [Google Scholar]
  6. Ravindra, K; Sokhi, R; van Grieken, R. Atmospheric polycyclic aromatic hydrocarbons: Source attribution, emission factors and regulation. Atmos. Environ 2008, 42, 2895–2921. [Google Scholar]
  7. Brown, J; Frame, G; Olson, D; Webb, J. The sources of the coplanar PCBs. Organohalogen Compounds 1995, 26, 427–430. [Google Scholar]
  8. Lohmann, R; Northcott, G; Jones, K. Assessing the contribution of diffuse domestic burning as a source of PCDD/Fs, PCBs, and PAHs to the UK atmosphere. Environ. Sci. Technol 2000, 34, 2892–2899. [Google Scholar]
  9. Jaward, F; Farrar, N; Harner, T; Sweetman, A; Jones, K. Passive air sampling of PCBs, PBDEs, and organochlorine pesticides across Europe. Environ. Sci. Technol 2004, 38, 34–41. [Google Scholar]
  10. Ikonomou, M; Sather, P; Oh, J; Choi, W; Chang, Y. PCB levels and congener patterns from Korean municipal waste incinerator stack emissions. Chemosphere 2002, 49, 205–216. [Google Scholar]
  11. Park, U; Kim, J; Masunaga, S; Kim, K. Source identification and concentration distribution of polychlorinated biphenyls in environmental media around industrial complexes. Bull. Environ. Contam. Toxicol 2009, 83, 859–864. [Google Scholar]
  12. Sabin, L; Maruya, K; Lao, W; Diehl, D; Tsukada, D; Stolzenbach, K; Schaff, K. Exchange of polycyclic aromatic hydrocarbons among the atmosphere, water, and sediment in coastal embayments of southern California, USA. Environ. Toxicol. Chem 2010, 29, 265–274. [Google Scholar]
  13. Muir, DCG; Grift, NP; Lockhart, WL; Wilkinson, P; Billeck, BN; Brunskill, GJ. Spatial trends and historical profiles of organochlorine pesticides in Arctic lake sediments. Sci Total Environ 1995, 160/161, 447–457. [Google Scholar]
  14. Muir, DCG; Omelchenko, A; Grift, NP; Savoie, DA; Lockhart, WL; Wilkinson, P; Brunskill, GJ. Spatial trends and historical deposition of polychlorinated biphenyls in Canadian midlatitude and Arctic lake sediments. Environ. Sci. Technol 1996, 30, 3609–3617. [Google Scholar]
  15. Cecinato, A; Mabilia, R; Marino, F. Relevant organic components in ambient particulate matter, collected at Svalbard Islands (Norway). Atmos. Environ 2000, 34, 5061–5066. [Google Scholar]
  16. Camus, L; Birkely, SR; Jones, MB; Børseth, JF; Grøsvik, BE; Gulliksen, B; Lønne, OJ; Regoli, F; Depledge, MH. Biomarker responses and PAH uptake in Mya truncata following exposure to oil-contaminated sediment in an Arctic fjord (Svalbard). Sci. Total Environ 2003, 308, 221–234. [Google Scholar]
  17. Wang, Z; Ma, X; Na, G; Lin, Z; Ding, Q; Yao, Z. Correlations between physicochemical properties of PAHs and their distribution in soil, moss and reindeer dung at Ny-Ålesund of the Arctic. Environ. Pollut 2009, 157, 3132–3136. [Google Scholar]
  18. Evenset, A; Christensen, GN; Skotvold, T; Fjeld, E; Schlabach, M; Wartena, E; Gregor, D. A comparison of organic contaminants in two Arctic lake ecosystems, Bjornoya (Bear Island), Norway. Sci. Total Environ 2004, 318, 125–141. [Google Scholar]
  19. Evenset, A; Christensen, GN; Carroll, J; Zaborska, A; Berger, U; Herzke, D; Gregor, D. Historical trends in persistent organic pollutants and metals recorded in sediment from Lake Ellasjoen, Bjornoya, Norwegian Arctic. Environ. Pollut 2007, 146, 196–205. [Google Scholar]
  20. Rawn, DFK; Lockhart, WL; Wilkinson, P; Savoie, DA; Rosenberg, GB; Muir, DCG. Historical contamination of Yukon Lake sediments by PCBs and organochlorine pesticides: Influence of local sources and watershed characteristics. Sci. Total Environ 2001, 280, 17–37. [Google Scholar]
  21. Stern, GA; Braekevelt, E; Helm, PA; Bidleman, TF; Outridge, PM; Lockhart, WL; McNeeley, R; Rosenberg, B; Ikonomou, MG; Hamilton, P; Tomy, GT; Wilkinson, P. Modern and historical fluxes of halogenated organic contaminants to a lake in the Canadian Arctic, as determined from annually laminated sediment cores. Sci. Total Environ 2005, 342, 223–243. [Google Scholar]
  22. Boitsov, S; Jensen, HKB; Klungsøyr, J. Natural background and anthropogenic inputs of polycyclic aromatic hydrocarbons (PAH) in sediments of the South-Western Barents Sea. Mar. Environ. Res 2009, 68, 236–245. [Google Scholar]
  23. Halsall, CJ; Barrie, LA; Fellin, P; Muir, DCG; Billeck, BN; Lockhart, L; Rovinsky, FY; Kononov, EY; Pastukhov, B. Spatial and temporal variation of polycyclic aromatic hydrocarbons in the Arctic atmosphere. Environ. Sci. Technol 1997, 31, 3593–3599. [Google Scholar]
  24. Hung, H; Kallenborn, R; Breivik, K; Su, Y; Brorström-Lundén, E; Olafsdottir, K; Thorlacius, JM; Leppänen, S; Bossi, R; Skov, H; Manø, S; Patton, GW; Stern, G; Sverko, E; Fellin, P. Atmospheric monitoring of organic pollutants in the Arctic under the Arctic Monitoring and Assessment Programme (AMAP): 1993–2006. Sci. Total Environ 2010, 408, 2854–2873. [Google Scholar]
  25. Stange, K; Klungsøyr, J. Organochlorine contaminants in fish and polycyclic aromatic hydrocarbon in sediments from Barents Sea. J. Mar. Sci 1997, 54, 318–332. [Google Scholar]
  26. Pulina, M; Burzyk, J; Burzyk, M. Carbon dioxide in the tundra soils of SW Spitsbergen and its role in chemical denudation. Pol. Polar Res 2003, 24, 243–260. [Google Scholar]
  27. Pulina, M; Krawczyk, W; Pereyma, J. Water balance and chemical denudation in the unglaciated Fugleberget basin (SW Spitsbergen). Pol. Polar Res 1984b, 5, 183–205. [Google Scholar]
  28. Hjelle, A. The Geology of Svalbard; Norsk Polarinstitutt: Oslo, Norway, 1993; pp. 1–163. [Google Scholar]
  29. Pękala, K. Morphogenetic processes and cover deposits of nunataks in the Hornsund area (SW Spitsbergen). Pol. Polar Res 1980, 1, 9–44. [Google Scholar]
  30. ISO 17993: Water Quality—Determination of 15 Polycyclic Aromatic Hydrocarbons (PAH) in Water by HPLC with Fluorescence Detection after Liquid–Liquid Extraction; International Organization for Standardization (ISO): Geneva, Switzerland, 2002.
  31. Wolska, L; Rawa-Adkonis, M; Namieśnik, J. Determining PAH and PCB in aqueous samples: Finding and evaluating sources of error. Anal. Bioanal. Chem 2005, 382, 1389–1397. [Google Scholar]
  32. Wolska, L. Miniaturised analytical procedure of determining polycyclic aromatichydrocarbons and polychlorinated biphenyls in bottom sediments. J. Chromatogr. A 2002, 959, 173–180. [Google Scholar]
  33. Mechlińska, A; Wolska, L; Namieśnik, J. Isotope-labeled substances in analysis of persistent organic pollutants in environmental samples. Trends Anal. Chem 2010, 29, 820–831. [Google Scholar]
  34. Rogowska, J; Mechlińska, A; Wolska, L; Namieśnik, J. Analytics of PAHs and PCBs in aquatic ecosystems. In Encyclopedia of Environmental Management; Jorgensen, SE, Ed.; Taylor & Francis Group: London, UK, 2012; in press. [Google Scholar]
  35. Rogowska, J; Wolska, L; Namieśnik, J. Impacts of pollution derived from ship wrecks on the marine environment on the basis of s/s “Stuttgart” (Polish coast, Europe). Sci. Total Environ 2010, 408, 5775–5783. [Google Scholar]
  36. Mechlińska, A; Wolska, L; Rogowska, J; Namieśnik, J. Sources and fate of PAHs and PCBs in the marine environment. Crit Rev Env Sci Technol 2011. in press. [Google Scholar]
  37. Senthil Kumar, K; Sajwan, KS; Richardson, J; Kannan, K. Contamination profiles of heavy metals, organochlorine pesticides, polycyclic aromatic hydrocarbons, and alkylphenols in sediment and oyster collected from marsh/estuarine Savannah GA USA. Mar. Pollut. Bull 2008, 56, 136–149. [Google Scholar]
  38. Budzinski, H; Jones, I; Bellocq, J; Pierard, C; Garrigues, P. Evaluation of sediment contamination by polycyclic aromatic hydrocarbons in the Gironde estuary. Mar. Chem 1997, 58, 85–97. [Google Scholar]
  39. Readman, J; Filmann, G; Tolosa, I; Bartocci, J; Villeneuve, J; Catinni, C; Mee, L. Petroleum and PAH contamination of the Black Sea. Mar. Pollut. Bull 2002, 44, 48–62. [Google Scholar]
  40. Baumard, P; Budzinski, H; Garrigues, P. PAHs in Arcachon Bay, France: Origin and biomonitoring with caged organisms. Mar. Pollut. Bull 1998, 36, 577–586. [Google Scholar]
  41. Donahue, WF; Allen, EW; Schindler, DW. Impacts of coal-fired power plants on trace metals and polycyclic aromatic hydrocarbons (PAHs) in lake sediments in central Alberta, Canada. J. Paleolimnol 2006, 35, 111–128. [Google Scholar]
  42. Tsapakis, M; Stephanou, E; Karakassis, I. Evaluation of atmospheric transport as a non-point source of polycyclic hydrocarbons in marine sediments of the Eastern Mediterranean. Mar. Chem 2003, 80, 283–298. [Google Scholar]
  43. King, A; Readman, J; Zhou, J. Dynamic behaviour of polycyclic aromatic hydrocarbons in Brighton marina, UK. Mar. Pollut. Bull 2004, 48, 229–239. [Google Scholar]
  44. Fang, GC; Chang, CN; Wu, YS; Fu, PPC; Yang, IL; Chen, MH. Characterization, identification of ambient air and Road dust polycyclic aromatic hydrocarbons in central Taiwan, Taichung. Sci. Total Environ 2004, 327, 135–146. [Google Scholar]
  45. Yunker, M; Macdonald, R; Vingarzan, R; Mitchell, R; Goyette, D; Sylvestre, S. PAHs in the Fraser River basin: A critical appraisal of PAH ratios as indicators of PAH source and composition. Org. Geochem 2002, 33, 489–515. [Google Scholar]
  46. Pancirov, RJ; Brown, RA. Analytical methods for polynuclear aromatic hydrocarbons in crude oils, heating oils and marine tissue. Proceedings of the 1975 Conference on the Prevention and Control of Oil Pollution, San Francisco, CA, USA, 25–27 March 1975; pp. 103–113.
  47. Hornbuckle, K; Robertson, L. Polychlorinated Biphenyls (PCBs): Sources, exposures, toxicities. Environ. Sci. Technol 2010, 44, 2749–2751. [Google Scholar]
  48. Rogge, WF; Hildemann, L; Mazurek, MA; Cass, GR; Simoneit, BRT. Sources of fine organic aerosol: 2. Non-catalyst and catalyst-equipped automobiles and heavy-duty diesel trucks. Environ. Sci. Technol 1993, 27, 636–651. [Google Scholar]
  49. Rogge, WF; Hildemann, LM; Mazurek, MA; Cass, GR; Simoneit, BRT. Sources of fine organic aerosol 3. Road dust, tire debris, and organometallic brake lining dust: Roads as sources and sinks. Environ. Sci. Technol 1993, 27, 1892–1904. [Google Scholar]
  50. Mandalakis, M; Tsapakis, M; Tsoga, A; Stephanou, EG. Gas particle concentrations and distribution of aliphatic hydrocarbons, PAHs, PCBs and PCDDyFs in the atmosphere of Athens (Greece). Atmos. Environ 2002, 36, 4023–4035. [Google Scholar]
  51. Ravindra, K; Bencs, L; Wauters, E; de Hoog, J; Deutsch, F; Roekens, E; Bleux, N; Bergmans, P; van Grieken, R. Seasonal and site specific variation in vapor and aerosol chase PAHs over Flanders (Belgium) and their relation with anthropogenic activities. Atmos. Environ 2006a, 40, 771–785. [Google Scholar]
  52. Guo, H; Lee, SC; Ho, KF; Wang, XM; Zou, SC. Particle-associated polycyclic aromatic hydrocarbons in urban air of Hong Kong. Atmos. Environ 2003, 37, 5307–5317. [Google Scholar]
  53. Khalili, NR; Scheff, PA; Holsen, TM. PAH Source fingerprints for coke ovens, diesel and gasoline engines, highway tunnels, and wood combustion emissions. Atmos. Environ 1995, 29, 533–542. [Google Scholar]
  54. Pandey, PK; Patel, KS; Lenicek, J. Polycyclic aromatic hydrocarbons: Need for assessment of health risks in India?—Study of an urban-industrial location in India. Environ. Monit. Assess 1999, 59, 287–319. [Google Scholar]
  55. Park, SS; Kim, YJ; Kang, CH. Atmospheric polycyclic aromatic hydrocarbons in Seoul, Korea. Atmos. Environ 2002, 36, 2917–2924. [Google Scholar]
  56. Jaffrezo, JL; Clain, MP; Masclet, P. Polycyclic aromatic hydrocarbons in the polar ice of Greenland—Geochemical use of these atmospheric tracers. Atmos. Environ 1994, 28, 267–294. [Google Scholar]
  57. Slater, JF; Currie, LA; Dibb, JE; Benner, BA. Distinguishing the relative contribution of fossil fuel and biomass combustion aerosols deposited at Summit, Greenland through isotopic and molecular characterization of insoluble carbon. Atmos. Environ 2002, 36, 4463–4477. [Google Scholar]
  58. Gabrielsen, GW; Skaare, JU; Polder, A; Bakken, V. Chlorinated hydrocarbons in glaucous gulls (Larus hyperboreus) in the southern part of Svalbard. Sci Total Environ 1995, 160/161, 337–346. [Google Scholar]
  59. Mehlum, F; Daelemans, FF. PCBs in Arctic seabirds from the Svalbard region. Sci Total Environ 1995, 160/161, 441–446. [Google Scholar]
  60. Wolkers, H; Lydersen, C; Kovacs, KM. Accumulation and lactational transfer of PCBs and pesticides in harbor seals (Phoca vitulina) from Svalbard, Norway. Sci. Total Environ 2004, 319, 137–146. [Google Scholar]
  61. Bang, K; Jenssen, BM; Lydersen, C; Skaare, JU. Organochlorine burdens in blood of ringed and bearded seals from north-western Svalbard. Chemosphere 2001, 44, 193–203. [Google Scholar]
  62. Bernhoft, A; Wiig, Ø; Skaare, JU. Organochlorines in polar bears (Ursus maritimus) at Svalbard. Environ. Pollut 1997, 96, 159–175. [Google Scholar]
  63. Skaare, JU; Larsen, HJ; Lie, E; Bernhoft, A; Derocher, AE; Norstrom, R; Ropstad, E; Lunn, NF; Wiig, Ø. Ecological risk assessment of persistent organic pollutants in the arctic. Toxicology 2002, 181–182, 193–197. [Google Scholar]
  64. Derocher, AE; Wolkers, H; Colborn, T; Schlabach, M; Larsen, TS; Wiig, Ø. Contaminants in Svalbard polar bear samples archived since 1967 and possible population level effects. Sci. Total Environ 2003, 301, 163–174. [Google Scholar]
  65. Brunström, B; Halldin, K. Ecotoxicological risk assessment of environmental pollutants in the Arctic. Toxicol Lett 2000, (112–113), 111–118. [Google Scholar]
Sensors 11 08910f1 1024
Figure 1. Location map for the sampling area: (a) surface water sampling points in the Fuglebekken basin (Kolondra L., Norway, Svalbard, Spitsbergen, Orthophotomap 1:10,000, NPI-TRomso University of Silesia); (b) major settlements in Svalbard and Polish Polar Station in Hornsund (labelled ‘Hornsund’) ( http://en.wikipedia.org/wiki/Template:Location_map_Svalbard).
Figure 1. Location map for the sampling area: (a) surface water sampling points in the Fuglebekken basin (Kolondra L., Norway, Svalbard, Spitsbergen, Orthophotomap 1:10,000, NPI-TRomso University of Silesia); (b) major settlements in Svalbard and Polish Polar Station in Hornsund (labelled ‘Hornsund’) ( http://en.wikipedia.org/wiki/Template:Location_map_Svalbard).
Sensors 11 08910f1 1024
Sensors 11 08910f2 1024
Figure 2. Flow chart of the procedure for preparing sea water samples for determining their PAH and PCB contents.
Figure 2. Flow chart of the procedure for preparing sea water samples for determining their PAH and PCB contents.
Sensors 11 08910f2 1024
Table
Table 1. The details of the sampling locations.
Table 1. The details of the sampling locations.
SitePosition
latitudelongitude
Tributary
B 177.01192215.562937
B 277.01394415.570209
B 377.01394415.570149
B 477.01241715.559140
B 577.01175815.540471
B 677.01264515.548105
B 777.01176715.536465
B 877.01156615.536151
B 977.01011515.532617
B 1077.00953515.532708
B 1177.00938815.532094
B 1277.00935115.536401
B 1377.00926315.539309
B 1477.00982415.541948
B 1577.01041215.544770
B 1677.00870215.548806
B 1777.00933215.550478
B 1877.00800515.552410
B 1977.00735115.548917
B 2077.00634315.552868
B 2177.00759315.543833
B 2277.00759215.543894
B 2377.00642015.548989
B 2477.00650115.548812
Stream water
B 2577.00585615.553388
Table
Table 2. The parameters of the Fuglebekken basin.
Table 2. The parameters of the Fuglebekken basin.
ParameterValue
Maximum height above sea level568.7 m
Minimum height above sea level0.0 m
Relative height above sea level568.7 m
Mean height of basin284.35 m
Slope of basin400.49‰
Slope of watershed90.27‰
Area of basin2.02 km2
Real area of basin2.64 km2
Length of basin2.1
Length of watershed6.3 km
Mean width of basin0.96
Form factor0.45
Compactness index1.24
Circularity ratio0.64
Elongation ratio0.76
Lemniscate index0.5
Table
Table 3. Measurement range, detection and quantification limits for the final determination of PAHs and PCBs.
Table 3. Measurement range, detection and quantification limits for the final determination of PAHs and PCBs.
AnalytesMeasuring range [ng/L]LOD [ng/L]LOQ [ng/L]
PCBs0.02–5600.0250.075
Naphthalene0.034–5600.0341.02
Acenaphthylene0.0041–5600.00410.0123
Acenaphthene0.0041–5600.00410.0123
Fluorene0.0018–5600.00180.0054
Phenanthrene0.0025–5600.00250.0075
Anthracene0.0078–5600.00780.0234
Fluoranthene0.014–5600.0140.042
PAHsPyrene0.028–5600.0280.084
Chrysene0.0022–5600.00220.0066
Benzo(b)fluoranthene0.014–5600.0140.042
Benzo(k)fluoranthene0.0023–5600.00230.0069
Benzo(a)pyrene0.0055–5600.00550.0165
Benzo(a)anthracene0.0017–5600.00170.0051
Indeno(1,2,3-cd)pyrene0.43–5600.431.29
Dibenz(a,h)anthracene0.014–5600.0140.042
Table
Table 4. Concentrations (ng/L) of PAHs in samples of water from Hornsund taken near the Polish Polar Station, Svalbard.
Table 4. Concentrations (ng/L) of PAHs in samples of water from Hornsund taken near the Polish Polar Station, Svalbard.
PAH compoundNapAcyAceFlPheAntFlrPyrChyBbFBkFBaPTotal PAHs
LOCATION
Tributary
B10.123.40.26<0.0018<0.002511<0.014<0.028<0.0022<0.014<0.0023<0.005515
B20.0340.270.0610.24<0.00254.42.0130.19<0.014<0.00230.220
B30.0662.51.32.3<0.002525<0.014<0.028<0.0022<0.014<0.0023<0.005531
B4<0.0341.71.92.0<0.0025532.84.2<0.0022<0.014<0.0023<0.005565
B55571.10.980.930.23311.8<0.0281.7<0.0149.0<0.0055603
B63101.71.5<0.0018<0.002526<0.014<0.028<0.0022<0.014<0.0023<0.0055339
B716<0.0041<0.0041<0.0018<0.0025<0.0078<0.014<0.028<0.0022<0.014<0.0023<0.005516
B8N = 13.0<0.00410.98<0.0018<0.0025<0.0078<0.014<0.028<0.0022<0.014<0.0023<0.00554.0
B90.51<0.004111.5<0.0025162.56.1<0.00221111<0.005550
B1011<0.0041<0.0041<0.0018<0.0025<0.0078<0.014<0.028<0.0022<0.014<0.0023<0.005511
B1542<0.00411.11.4<0.0025141.5<0.028<0.0022<0.014<0.0023<0.005560
B1711<0.00413.31<0.002567<0.014<0.028<0.0022<0.014<0.0023<0.005583
B18110<0.0041<0.0041<0.0018<0.0025<0.0078<0.014<0.028<0.0022<0.014<0.0023<0.0055110
B198.8<0.0041<0.0041<0.0018<0.0025<0.0078<0.014<0.028<0.0022<0.014<0.0023<0.00558.8
B20<0.034<0.00410.94<0.0018<0.00257.5<0.014<0.028<0.0022<0.014<0.0023<0.00558.4
B2213<0.00410.55<0.0018<0.00254.51.4<0.028<0.0022<0.014<0.0023<0.005520
Stream water
FuglebekkenN = 700.741.50.0550.00940.0740.230.0990.520.0190.040.0140.0253.3

Naphthalene (Nap), Acenaphthylene (Acy), Acenaphthene (Ace), Fluorene (Fl), Phenanthrene (Phe), Anthracene (Ant), Fluoranthene (Flr), Pyrene (Pyr), Chrysene (Chy), Benzo(b)fluoranthene (BbF), Benzo(k) fluoranthene (BkF), Benzo(a)pyrene (BaP).

Table
Table 5. Concentrations of PAHs in abiotic and biotic samples from Svalbard.
Table 5. Concentrations of PAHs in abiotic and biotic samples from Svalbard.
LocationObjectConcentrationReferences
[ng/g] *
Abiotic environmentSvalbard
Ny-ÅlesundSedimentsΣ15PAHs 27–711 (lakes) (dw)[2]
Σ15PAHs 27–34 (coastal area) (dw)
Ambient particulate matterΣPAHs 0.6–2.0 ng/m3[15]
Surface soilΣ16PAHs 37–324 (dw)[17]
MossΣ16PAHs 158–244 (dw)
Reindeer dungΣ16PAHs 49–340 (dw)
WijdefjordenSedimentsΣ16PAHs 36 (fjords, tidal plains) (dw)[18]
Σ16PAHs 429 (lakes) (dw)
AdventfjordenTotal PAH 0.94 (ww)[16]
LocationSpeciesTissueConcentration
Biotic environment[ng/g] *
Svalbard
AdventfjordenBivalvesCTotal PAH 0.20 (lw)[16]

*concentrations reported as means or ranges of means of dry weight (dw), wet weight (ww) or lipid weight (lw); C—clam.

Table
Table 6. PAH indicator ratios for surface water samples from Svalbard and the potential sources of the emission of these compounds.
Table 6. PAH indicator ratios for surface water samples from Svalbard and the potential sources of the emission of these compounds.
PAH ratioNap/PhePhe/AntAnt/(Ant+Phe)BaA/ChyBaA/(BaA+Chy)Flr/PyrFlr/(Flr+Pyr)LMW/HMW *Fl/(Fl+Pyr)BaP/(BaP+Chy)BbF/BkF
LOCATION
Tributaries
B1–B242,4760.0006680.999 (0.993–1)––0.412 (0.156–0.669)0.638 (0.135–1)56.4 (1.26–102)0.648 (0.0181–1)0.5091.015
Main stream water
Fuglebekken96 (0.409–595)0.771 (0.0207–0.908)0.851 (0.524–1)0.846 (0.0224–1.20)0.547 (0.0219–0.546)0.628 (0.0830–2.04)0.526 (0.0766–0.671)14.2 (0.0261–241)0.755 (0.00431–1)0.773 (0.235–1)3.97 (0.140–8.19)
SOURCE
Combustion>1[6]<10[38,39]>0.1[42]>1[43]>0.2[45]>1[38]0.4–0.5[45]<1[38,47]
>0.9[43]>0.5[45]
Petrogenic<1[6]>10[38]<0.1[42]<1[43]<0.2[45]<1[38]0.22[45]>1[38,47]
>15[39]<0.4[43]
>25[40]
Petrol emissions0.47–0.59[3,44]0.43[41]<0.5[44,48–51]0.73[52,53]1.07–1.45[3]
Diesel>0.5[44,48–51]0.5[52,53]>0.5[54,55]
Coal emissions1.05–1.17[3,44]0.58[41]3.53–3.87[3]
Fuel oil50[41]0.9[46]

*LMW/HMW—Low Molecular Weight/High Molecular Weight.

Table
Table 7. Interpretation of measurement data regarding the main sources of PAH emission found in water samples from Svalbard.
Table 7. Interpretation of measurement data regarding the main sources of PAH emission found in water samples from Svalbard.
PAH ratioFuglebekken [%]B1–B24 [%]Source
Nap/Phe>191100combustion
<19-petrogenic
Phe/Ant<10100100combustion
Ant/(Ant+Phe)>0.1100100combustion
BaA/Chy>171-combustion
<0.429-petrogenic
BaA/(BaA+Chy)>0.290-combustion
<0.210-petrogenic
Flr/Pyr>115-combustion
<185100petrogenic
Flr/(Flr+Pyr)>0.458100combustion
<0.442-petrogenic
LMW/HMW<164100combustion
>136-petrogenic
Fl/(Fl+Pyr)<0.52743gasoline
>0.57357diesel
BaP/(BaP+Chy)0.7371-gasoline
0.529100diesel
BbF/BkF1.07–1.4525-gasoline
>0.575100diesel
Table
Table 8. Concentrations (ng/L) PCBs found in samples of water taken from catchment area at Hornsund, near the Polish Polar Station, Svalbard.
Table 8. Concentrations (ng/L) PCBs found in samples of water taken from catchment area at Hornsund, near the Polish Polar Station, Svalbard.
PCB compound
LOCATIONPCB 28PCB 52PCB 101PCB 118PCB 138PCB 153PCB 180Total PCBs
Tributary
B28.56.25.11.88.58.01048
B3<0.025<0.0256.03.8<0.025<0.025<0.0259.8
B5<0.0252.01018123<0.025<0.025153
B7N = 1<0.0253.93.63.5<0.025<0.025<0.02511
B8<0.025<0.025244871<0.025<0.025143
B9<0.025<0.0252672308<0.025<0.025406
B10<0.0254.2<0.025<0.025<0.025<0.025<0.0254.2
B11<0.0255.2<0.025<0.025<0.025<0.025<0.0255.2
B12<0.0252.3<0.025<0.025<0.025<0.025<0.0252.3
B14<0.0254.1<0.025<0.025<0.025<0.025<0.0254.1
B15<0.0251.94.67.3<0.025<0.025<0.02514
B16<0.0253.9<0.025<0.025<0.025<0.025<0.0253.9
B17145.52.63.5<0.025<0.025<0.02526
B18<0.0255.332.23.4<0.025<0.025<0.02511
B19<0.0256.45.6<0.02538<0.025<0.02550
B20<0.02529<0.025<0.025<0.025<0.025<0.02529
B21<0.0255.2<0.025<0.025<0.025<0.025<0.0255.2
B22<0.02526<0.025<0.0258.7<0.025<0.02535
B24<0.025102.5<0.025<0.025<0.025<0.02513
Stream water
FuglebekkenN = 700.510.140.940.960.390.640.714.3

There are no literature data on the determination of PCBs in surface waters on Svalbard. Nonetheless, analyses of PCBs in other compartments of the environment have been done far more often. PCBs have been found in bottom sediments (Ny-Ålesund, Wijdefjorden) [2,18], and also in the biotic environment: common eider [56], kittiwake [56], glaucous gull [56–58], black guillemot [25,59], eider [59], harbour seals [60], milk [60], pups [60], bivalves [16], Brünnich’s guillemot [59], ringed seals [61], bearded seals [61] and polar bears [61–64] (Table 9).

Table
Table 9. PCB concentrations in the abiotic and biotic environment in Svalbard.
Table 9. PCB concentrations in the abiotic and biotic environment in Svalbard.
LocationObjectConcentration [ng/g] *Refs.
Abiotic environmentSvalbard
Ny-ÅlesundSedimentsΣ15PCBs 0.18–13 (lakes) (dw)[2]
Σ15PCBs 0.33–0.42 (coastal area) (dw)
WijdefjordenΣ7PCB <0.9–5.5 (fjords, tidal plains) (dw)[18]
Σ7PCB <0.1–14.6 (lakes) (dw)
Biotic environmentSvalbard
Ny-ÅlesundCommon eider, Kittiwake, Glaucous gullL,B,FΣ19PCB 0.8–24 976 (ww)[56]
BarentsburgGlaucous gullLΣ32PCB 386–2 347 (ww)[57]
LongyearbyenGlaucous gull, Black guillemot, EiderLTotal PCB 40–77 750 (ww)[59]
NordaustlandetGlaucous gull, Black guillemot, EiderLTotal PCB 10–21 130 (ww)
Prins Karls ForlandHarbour seals (males, females), Milk, PupsBlΣPCBs 271.6–2201.1 (lw)[60]
StorfjordenBrünnich’s guillemotLTotal PCB 40–180 (ww)[59]
KongsfjordenRinged and Bearded seals (males, females)BdΣPCBs 159/1–624/8 (lw)[61]
Southern, south-eastern, northern partsPolar bearsS,BcΣPCBs 2220–80 300 (lw)[62]
Southern, south-eastern partPolar bearsBpΣPCBs 21–228 (ww)[63]
Eastern partPolar bearsBpΣPCBs 214,4 (ww)[64]
Southern partGlaucous gull, GuillemotsL,B,K,M, eggsΣ21PCB 118–32 300 (ww)[58]
Western partBlΣ102PCB 1130–5 250 (lw)[25]

*concentrations reported as means or ranges of means of dry weight (dw), wet weight (ww) or lipid weight (lw); L-Liver, B-Brain, F-Fat, M-Muscle, K-Kidney, Bl-Blubber, C-Clam, S-Subcutaneous, Bc-Blood cells, Bp-Blood plasma, Bd-Blood.

Table
Table 10. Calculated PCB and PAH loads transported in the Fuglebekken basin.
Table 10. Calculated PCB and PAH loads transported in the Fuglebekken basin.
Load
Analytesng per secondμg per hourmg per day
Nap5.1180.44
Acy10370.89
Ace0.381.40.033
Fl0.0650.230.0056
Phe0.511.80.044
Ant1.65.60.14
Flr0.682.50.059
Pyr3.6130.31
Chy0.130.470.011
BbF0.280.990.024
BkF0.0990.350.0085
BaP0.170.620.015
Total PAHs1154129.9
PCB 283.5120.30
PCB 520.692.50.060
PCB 1016.2220.54
PCB 1186.9250.60
PCB 1382.89.90.24
PCB 1534.1150.36
PCB 1804.8170.42
Total PCBs20774518

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MDPI and ACS Style

Polkowska, Ż.; Cichała-Kamrowska, K.; Ruman, M.; Kozioł, K.; Krawczyk, W.E.; Namieśnik, J. Organic Pollution in Surface Waters from the Fuglebekken Basin in Svalbard, Norwegian Arctic. Sensors 2011, 11, 8910-8929. https://doi.org/10.3390/s110908910

AMA Style

Polkowska Ż, Cichała-Kamrowska K, Ruman M, Kozioł K, Krawczyk WE, Namieśnik J. Organic Pollution in Surface Waters from the Fuglebekken Basin in Svalbard, Norwegian Arctic. Sensors. 2011; 11(9):8910-8929. https://doi.org/10.3390/s110908910

Chicago/Turabian Style

Polkowska, Żaneta, Katarzyna Cichała-Kamrowska, Marek Ruman, Krystyna Kozioł, Wiesława Ewa Krawczyk, and Jacek Namieśnik. 2011. "Organic Pollution in Surface Waters from the Fuglebekken Basin in Svalbard, Norwegian Arctic" Sensors 11, no. 9: 8910-8929. https://doi.org/10.3390/s110908910

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