//0?*0OO ?2
KJELLER REPORT
ATMOSPHERIC DEPOSITION OF TRACE ELEMENTS IN NORWAY STUDIED BY MEANS OF MOSS ANALYSIS
by E. Steinnes
INSTITUTT FOR ATOMENERGI INSTITUTT FOR ATOMENERGI KJELLER RESEARCH ESTABLISHMENT Kjeller, Norway
ATMOSPHERIC DEPOSITION OF TRACE ELEMENTS IN NORWAY STUDIED BY MEANS OF MOSS ANALYSIS by E. Steinnes
Kjeller, February 1977 ISBN 82 7017 009 7 ABSTRACT
The atmospheric deposition of 28 elements in different parts of Norway was studied by means of moss analysis. The species Hylocomium splendens was selected after a comparison of different species. For several elements large regional differences were found. The highest concentration of these elements were found in the southernmost part Of the country and in places near the west coast with high annual precipitation. The lowest values were found in places with low annual precipitation in Eastern Norway and the interior parts of the more northerly parts of the country. Within each region the highest deposition was observed in places with high annual precipitation. For the elements Pb, Sb, As, and Se the observed concentration range amounted to a factor of about 20. In the case of Ag, Cd, Cs, and V the range was smaller, but still amounting to a factor of 10 or more. A lower but still distinct spread was observed for Cr, Mo, Cu, and Zn. For all these elements long distance transport from sources in the densely populated and heavily industrialized parts of Europe probably are of importance for the observed distribution. ATMOSPHERIC DEPOSITION OF TRACE ELEMENTS IN NORWAY STUDIED BY MEANS OP MOSS ANALYSIS BY E. Steinnes
1. INTRODUCTION The atmospheric transport of pollutants over very long distances is now a well established fact. The first convincing evidence came from studies of radioactive fall-out from nuclear weapon explosions. More recently long-distance transport of heavy metals has been documented as well. Analyses of ice cores from glaciers situated in remote areas, clearly indicated that th« airborne supply of elements such as lead (1, 2) and cadmium (2) to these areas has increased very distinctly during the last couple of decades as compared with previous centuries. Analyses of air particulates collected at a remote location in Northern Norway (3)/ showed that the chemical composition of aerosols supplied by southerly winds was very similar to that observed for typiral pollution aerosols collected in Central Europe. Perhaps the most convincing evidence of heavy metal transport to Scandinavia from external sources is the study by Riihling and Tyler (4, 5), who showed by means of moss analysis that the deposition of certain heavy metals in the southern and south-western parts of the Scandinavian peninsula was distinctly greater than in the northernmost part of the area. Their sampling network was most extensive in the case of Sweden, but also included certain areas of Norway. Their analyses which were based on samples collected during the period 1968 - 1970, indicated that the atmospheric deposition of lead and cadmium was almost an order of magnitude higher in the southernmost part of Norway than in the far north. Similar but less distinct concentration gradients were indicated for mercury, chromium, nickel, copper, and zinc. As there are no major industrial sources of lead and cadmium discharge in girlandet, it seems quite evident that sources outside Scandinavia are mainly responsible for the observed pattern. This rather alarming information seemed tc call for more work on this matter. Mosses are useful indicators of atmospheric pollutants, because they have a very high capacity to retain many inorganic ions, and because minerals enter these plants almost entirely through the air. Lichens possess similar properties, and have turned out to be useful especially in studies of radioactive fall-out. Frou. the available literature it was indicated that several species might be advantageously used in a survey of the atmospheric deposition of trace elements in Norway. fJuhliny and Tyler used the moss Hylocomium splendens in the study mentioned above. In a similar investigation in Finland (6) the bog moss Sphagnum fuscum was used. Reindeer lichens, especially Cladonia alpestris, have often been used in radioactive fall-out studies, and might also turn out to be efficient in the case of trace elements. Th-.- lichen Hypogymnia physodes, which was recently shown to be a very good indicator for atmospheric mercury (7), could also be an interesting alternative. All these species are abundant in most parts of Norway. It was decided to collect samples of all four species, and then select the most suitable one for an extended study on the basis of a comparison with respect to a limited number of elements.
2. EXPERIMENTAL 2.1 Sampling The sampling sites used in this work are listed in Table T, along with data on the mean annual precipitation- As indicated on the map in Fig. 1, the sampling sites show a fairly even distribution all over the country. A somewhat denser network was used in the southernmost part of the country, in anticipation of higher deposition of certain trace elements in this area than elsewhere in the country (5). Sampling sites in the close proximity of industrial plants or larger population centra were avoided. Wherever possible, sites within relatively short distance showing large variation in annual precipitation were included,- in order to get some information about the possible relation between trace element deposition and precipitation. All samples were collected during the month of July 1976. Each sample typically consisted of five sub-samples taken within 4 2 an area of 10 m or less. The material was always sampled at a distance of at least 300 m from roads or built-up areas. The material was collected in double polyethylene bags, and disposable 3
polyethylene gloves were used in the sampling as well as in the subsequent handling of the samples. In most cases the sampling took place in woodland areas. Except for Hypogymnia physodes the samples were taken outside the crown projection of trees. Hyiocomium splender.s was found in all the samp].ing sites involved. Samples of Hypogymnia physodes were obtained at all sites excepting No. 63, and were collected on birch trees. Sphagnum fuscum was difficult to find in some cases, and samples of Sphagnum nemoreum or Sphagnum apiculatum were taken instead. Similarly Cladonia alpestris was replaced by Cladonia rangiferina or Cladonia silvatica in some cases, especially at sites near the coast. In some sites more than one species of Sphagnum or Cladonia was collected for the sake of comparison. During the collection of Sphagnum samples the upper 8 - 10 cm of the moss carpet were taken. In the case of Cladonia the top ^ 5 cm of the plants, were employed. In the laboratory the samples were dr^ed to constant weight at room temperature, and then foreign matter was carefully removed. After additional mixing of each sample, sub-samples were taken for trace element determination either by instrumental neutron activation analysis (INAA) or by atomic absorption spectrophotometry (AAS).
2.2 Neutron activation analysis Aliquots of 0.2 - 0.3 g of each sample jere irradiated in the JEEP II reactor at a thermal neutron flux of about 13 -2 -1 1.5 • 10 n cm s . After appropriate decay intervals the samples were assayed by Ge(Li) y-spectrometry using coaxial Ge(Li) detectors with associated electronics, interfaced to a small digital computer. Standards for each element to be determined were irradiated, and the quantitative determinations were based on peak areas calculated according to methods described in the literature (B, 9). Two different procedures were employed:
A, Determination via short-lived nuclides according to the following sequence: 30 sec. irradiation - 12. min. delay - 5 min. counting. The samples and standards were irradiated one by one in sealed polyethylene tubes, assuming constant 4
neutron flux. The elements determined in this manner vere Al, V, Mn, Cl, and I.
B. Determination via more long-lived nuclides (t, > 12 h.). In this case a 20-hours1 irradiation in sealed quartz ampoules was used. The samples were removed from the quartz ampoules, and counted after three days and three weeks respectively. On the basis of this procedure the following 21 elements were determined: Na, K, Br, As, Sb, Hg, La, Sm, Mo, U, Th, Fe, Co, Rb, Cs, Ag, Se, Cr, and Sc.
2.3 Atomic absorption spectrophotometry For this analysis 2-g portions were weighed into 50-ml Erlenmeyer flasks, and digested with 20 ml of concentrated HNCU and 5 ml of concentrated HC10. until all organic matter had been destroyed. This usually took 1-2 days. After evaporation of excess HNCU the residual solution was diluted to 25 ml with water, and analyzed by an atomic absorption spectrophotometer according to procedures described by the manufacturer of the instrument (10). A blank was run along with every ten samples. The conventional flame technique using air/acetylene was ured for the determination of lead, zinc, and copper, while cadmium was determined by flameless AAS using a graphite furnace. The standard solutions were prepared with the same amounts of acids as for the sample solutions.
3. RESULTS AND DISCUSSION 3.1 Uptake of trace elements in different species In order to compare the applicability of each of the species concerned for trace element deposition studies all the collected samples were analyzed with respect to the four elements Pb, Zn, Cd, and Cu. In Table II concentration factors relative to Hylocomium splendens are presented. Separate values have been calculated for each of the major regions of the country. In the case of Sphagnum values for vanadium are also given. The usefulness of a certain species for atmospheric deposition studies does not depend only on a high uptake capacity for the elements concerned, but also on its ability to demonstrate concentration d-f f r-rences. This aspect was studied by selecting 5
five sampling sites where high levels of the four elements are evident, calculating the average concentration for each species, and dividing each value by the corresponding value based on five sampling sites with a generally low level of all elements. The results of this test are shown in Table III. It is clear that the content in Hypogymnia physodes is significantly higher than in the other species, at least for Pb, Zn, and Cd, but the relative concentration factor shows a large variation for the four elements. Cladonia shows the lowest content, the relative concentration factor being higher for Zn and Cd than for the other elements. The content in Sphagnum is slightly lower than that of Hylocomium, and the relative concentration factor is quite constant for all the elements studied. It may be noted on this point that no appreciable difference in the uptake of any of the four elements between different species of Cladonia or Sphagnum was indicated from the cases where comparative analyses could be made. The calculated concentration factors for different regions showed quite low variation except for Kypogymnia physodes, in which case the relative concentration factor showed a variation of more than a factor of 2 in seme cases. This indicates that the uptake of airborne trace elements in this species is not only dependent on the incoming flux of the element, but also on other factors, such as the local meteorological conditions or differences in growth rate. The use of Hypogymnia physodes was therefore disregarded. From Tables II and III it is also clear that the Cladonia species are less suitable than the messes involved, at least as far as the present elements are concerned. The uptake properties of Hylocomium and Sphagnum appear to be quite similar, but a small tendency in favour of Hylocomium is indicated. Additional evidence pointing in the same direction is that Hylocomium was found at all sampling sites, is easily identified, and permits a more certain estimation of the integrated exposure time. The subsequent work was therefore based on Hylocomium splendens.
3.2 Regional distribution of trace elements Data showing the content of 27 elements in samples of Hylocomium splendens are given in Table IV. It is clear that large regional differences in atmospheric deposition exist for many elements. Evidently a considerable number of elements 6
exhibit a similar trend to that previously indicated for Pb and Cd (4,5). The following general observations can be made for this group of elements:
a) The maximum concentrations are observed in the region of Sørlandet, indicating supply from sources out of Norway predominantly by southerly winds. b) High concentrations are also observed in places along the west coast with high annual precipitation, all the way up to Lofoten (e.g. sampling points no. 32, 36, 53, and 56). This indicates that considerable input of pollution-derived trace elements may take place also through westerly winds. Natural sources may, however, also be of some consequence for some elements. c) Within each local area sampling points with high annual precipitation generally show higher concentration of the elements concerned than points with lower precipitation. The most typical example of this is perhaps points 14 and 15, where differences of a factor of 2 or more are evident for several elements even though the distance between the two points is only 40 km. Other typical cases are points no. 30 - 31, 36 -37, and 56 - 57. d) The lowest concentrations are found in the northern part of østlandet and in the interior regions of Møre and Trøndelag and Northern Norway. Most of the places showing low concentrations of the elements concerned, have low levels of annual precipitation. e) There is a slight indication that lower amounts of heavy metals are supplied to the coastal districts of Møre and Trøndelag than to places further south or further north along the cost. f) Except for samples 22, 64, and 55, there is no indication that the results obtained are much affected by local pollution sources. 7
g) The general trend from the work of Ruhling and Tyler (4.5) for elements belonging to this group of elements is generally verified in the cases where comparison of data is possible. There seems to be a slight trend towards increasing levels for some elements in Finnmark since 1968 when the material of Ruhling and Tyler was collected.
h) Riihling and Tyler indicated a straight south-north concentration gradient for the geographical distribution of Pb and Cd in Norway (4.5). As indicated above, the distribution trend for this type of elements appears to be appreciably more complex, the annual precipitation evidently being an important factor.
Not all elements studied exhibit the type of geographical distribution pattern described above, which will be referred to as the Pb-type distribution in the subsequent text. Some elements show a distribution mainly governed by supply from the marine environment, while others show a fairly even distribution all over the area. For certain elements Hylocomium sp.1 andens gives no reliable measure of deposition because of considerable wash-out in samples collected near the coast. In the following the elements investigated are discussed separately. In order to express the extent of fractionation between areas with a high supply of trace elements and those leaL.t affected by airborne supply, the H/L ratio defined in Table III has been adopted.
3_12_.l__Alkali_ elements
The observed sodium distribution is consistent wiLh a marine source for this element. The analysis is, however, sensitive to contribution from soil particles, which are rich in sodium. This may explain the somewhat higher sodium level found in this work for inland areas compared to that reported by P'ihling and Tyler (4) . The potassium level is quite uniform all over the country and confirms the values reported by Ruhling and Tyler (4). Also for rubidium no distinct regional differences are evident. Samples taken at places with high annual precipitation or close to the coast are depleted in rubidium, which is probably due to a combined effect of wash-out and replacement by sodium and 8
magnesium present in high concentrations from the sea salt. For caesium, which is the most volatile of the alkali elements, a distribution of the Pb-type is indicated, "with a H/L ratio of 7.0.
3.2.2 _Aluminium
The general level of this element is similar in all major regions, but the variation between single samples is quite large. A high content cf aluminium in a sample is a good indication of soil contamination.
a e m s å^~é.^'å ££f£ 9to^i_li^hophilici_ iS ÉD£ (§9£_ka^_SmJ._Thi_arid _U)_ These elements show a similar trend. If a few samples in the low-precipitation group, apparently soil contaminated, are disregarded, H/L ratios of the order of 2 are indicated. Thus even for these elements the airborne supply may be greater in Sørlandet than in other parts of the country.
2^2_14__yanadium
With a few exceptions the vanadium results, as shown in Fig. 2, are consistent with a Pb-type distribution, with a H/L ratio of 6.2. It seems reasonable to ascribe the excess vanadium in the southernmost part of the country to the burning of oil, predominantly outside the country.
3i2i5__Chromiurn
Also for this element a Pb-type distribution is indicated, but to a lesser extent than for vanadium, the calculated H/L ratio being 3.1. The level of chromium in this work is about 60% of that reported by Riihling and Tyler (4, 5), but the general distribution trend is similar.
3^2^6 Molybdenum
This is another case of an apparent Pb-type distribution. It was not possible to determine this element in all samples, partly because of a nuclear interference from uranium, and a lower limit of 0.10 ppm was applied. The H/L ratio is > 3.7, probably as high as 5. 9
3_. 2^7 Manganese
The manganese concentration, showing a fairly uniform level at about 300 ppm in the interior areas of the country, drops to values below 100 ppm at the coast. As pointed out by Ruhling and Tyler (4) , the retention capacity of manganese in mosses is rather low, and the element may be lost by exchange with sodium and magnesium ions. Thus the analysis of moss samples does not appear to be useful for studies on the deposition of airborne manganese.
3_.2_.8 Iron
Although the iron results in part tend to be obscured by soil contamination, the present work seems to indicate a slight tendency towards a Pb-type distribution also for iron, with a H/L ratio of about 2. This trend is in agreement with that found by Ruhling and Tyler {4, 5), The absolute levels, however, show slight disagreement. While Siihling and Tyler reported 1150 ppm as a typical value for Sørlandet, the present work indicates a value of 750 ppm, which was obtained both by neutron activation and atomic absorption.
3i2i9__Cobalt
The cobalt distribution is rather similar to that of iron. The concentration level found in this work is about 2.5 times lower than that reported by Ruhling and Tyler. Presumably neutron activation analysis should be more suitable for cobalt determinations at the concentration level concerned than flame atomic absorption.
^j.2^.10__Copper
The copper levels, shown in Fig. 3, are very similar to those reported by Ruhling and Tyler (4, 5). The H/L ratio for copper is 2.7. An abnormally high copper value was recorded in sample 22. As this sample was taken only 15 km as the crow flies from Kristiansand, the high copper content is likely to originate partly from a metal-refinery situated in that town, using copper-.;ickel matte as raw material. The high copper values for samples 64 and 65 may be associated with similar industry situated on the Sovjet side of the border. 10
i.i2_.ll__Silyer
This element also shows a Pb-type distribution, the H/L ratio being 6.4.
3^2^12 Zinc
The data for zinc from this work, shown in Fig. 4, are similar to those of Ruhling and Tyler, but somewhat more distinct regional differences are indicated from this work, as indicated from the calculated H/L ratio of 2.8.
3^2;13__Cadmium
The distribution of cadmium is shown in Fig. 5. Also for this element the present work confirms the findings of Ruhling and Tyler, except that the general level is found to be about 301 lower in this work. The H/L ratio of 7.2 is one of the highest observed.
2^.2^14__Mercury
The present result might be systematically low due to possible loss of mercury when opening the quartz ampoules. The results obtained are, however, in very good agreement with those of Ruhling and Tyler. The H/L ratio is only 1.8, indicating a more uniform airborne supply of mercury than for other volatile metals.
3i2i15__Lead Lead (Fig. 6> is the element showing the largest fractionation, the H/L ratio being 12.9. Corresponding results were obtained by Ruhling and Tyler (4, 5) and by Hvatum (12) in a study of ombrogenous surface peat in different parts of Norway. As emphasized by Ruhling and Tyler, there is stiong evidence that a major part of the excess lead observed in the south-western parts of Norway is imported from the more heavily industrialized and densely populated part of Europe.
3.2.16 Arsenic and_antimony
The distribution pattern of antimony, shown in Fig. 7, appears to be very similar to that observed for lead. The H/L 11
ratio for antimony is 11.3. Although less distinct, the distribution of arsenic, shown in Fig. 8, is also of the Pb- type, the H/L ratio beir: 4.5. it is possible that some of the airborne arsenic may originate from naturally occuring processes, such as volcanic eruptions.
3^.2^27 Selenium Also this elerentshows a large fractionation of the Pb- type (Fig. 9), with a H/L ratio of 9.0. Previous work in the author's laboratory on the regional distribution of selenium in Norwegian forest soils indicated that selenium in the soil is ,:o a great extent supplied through the precipitation. This selenium is likely to originate from natural sources (13, 14). If the results for selenium and antimony in Table IV ^ e compared, it is observed that the levels are similar : the far south (stations 20 - 26) and in the interior districts, while distinctly higher selenium levels are observed at most coastal sites (e.g. 36, 42, 43, 52, 53, 56, 57, 62, and 63). This indicates that a contribution from natural sources of airborne selenium can be identified even in the present material.
3^2^18 Chlorine_and_bromine
Both elements show a distribution indicating marine supply. This trend is more distinct in the case of bromine (Fig. 10), because chlorine shows a tendency to be washed out in cases of high precipitation (e.g. samples, 31, 36, and 42). Hylocomium splendens may therefore be a useful indicator of the relative deposi tion of brcmine, but not of chlorine. This conclusion is supported by the fact that Sphagnum samples that were analyzed with respect to these elements, showed quite similar results for bromine, while the chlorine data were about a factor of 2 - 10 higher and showed only moderate correspondence with the chlorine data for Hylocomium.
4. SOME CONCLUDING REMARKS Several years ago it was already clearly indicated that the heavy metals lead and cadmium are deposited in much higher amounts in the south-western part of Norway than in other parts of the country. The present work has extended the list of 12
potentially hazardous elements showing a similar type of distribution, and indicates that relatively large amounts of such elements may be deposited also in several places in more northern latitudes with high annual precipitation. The use of Hylocomium splendens in this kind of work appears to be very useful. In order to get a more complete survey of the regional deposition of these elements in Norway and investigate the contribution of local air pollution sources in this pictuie, extended work including a far more detailed sampling network is necessary.
5. REFERENCES
1. Murozomi, M.f Chow, T.J., and Patterson, C: Geochim. Cosmochim. Acta 3_3, 1247 (1969) .
2. Jawrnwski, Z., Bilkiewicz, J., Dobosz, E., Grzybowska, D., Kownacka, L. .. and VJronski, Z.: Environmental. Surveillance around Nuclear Installations, Vol. I, I.A.E.A., Vienna, 1974, p. 40 3.
3. Rahn, K.A., private communication.
4. Riihling, A., and Tyler, G. : Nedfallet av tunga metaller over Skandinavien. Unpublished report, Avdelningen for ekologisk botanik. Lunds Universitet, 1972.
5. Ruhling, A., and Tyler, G.: Water, Air, and Soil Pollution 2, 445 (1973).
6. Pakarinen, P., and Tolonen, K.: Ambio 5, 38 (1976). 7. Steinnes, E., and Krog, H.: Oikos, in press.
8. CovcU, D.F.: Anal. Chem. 3j.< 1785 (1959).
9. Sterlinski, S.: Anal. Chem. 40, 1995 (1968).
10. Analytical Methods for Atomic Absorption Spectrophotometry. Perkin-Elmer Corp., Norwalk, Conn. (1973).
11. Nedbøren i Norge 1895 - 1943. Det norske meteorologiske institutt, Oslo (1949).
12. Hvatum, 0.0.: Teknisk Ukeblad, Oslo, 118, no. 27, p. 40 (1971). 13
13. Låg, J., and Steinnes, E. : Ambio 3_, 237 (19T4) .
14. Låg, J., and Steinnes, E.: To be published.
ESte/SiH 12.1.77 TABLE I
SAMPLING S:L'TE S SELECTED FOR THE PRESENT WORK
Lati.tud e Longitude Annual . . • ^ ... x} Sampling site N E precipitation Region No. Location o ' o ' rim østlandet 10 Mangen 59 5 5 11 40 -. 700 11 Rena 61 10 11 20 7 30 12 Tynset 62 : 5 10 45 350 13 Lesja 62 7 8 50 360 14 Nesbyen 60 35 9 5 450 ]5 Gulsvik 60 22 9 33 810 16 Nissedal 59 11 8 30 •v. 750 Sørlandet 20 Krabbesund 58 40 9 40 •>. 900 21 Vegårshei 58 45 8 51 1370 22 Ulvøysund 58 7 8 14 •*. 900 23 Birkeland 58 20 8 15 14 70 24 Hornnes 58 33 7 4 5 •v 12 50 25 Lindesnes 57 59 7 4 ". 900 26 Vigmostad 58 12 7 21 •>- 1650 Ves 11 ^. ndc t 30 Eigerøy 58 27 5 54 •i. 1000 31 Ørsdalen 58 39 6 22 2330 32 Børtveit 59 53 5 31 2830 33 Fitjar 59 55 5 18 1490 3 4 Breistølen 61 1 8 3 5S0 35 Kaupanger 61 11 7 13 •v 800 36 Hovlands- dal 61 14 5 26 3170 37 Gloppen 61 48 6 10 1040 M*':c -..-d '!:-• •ndrlag 40 Ørsta 62 9 6 17 1950 41 Valldal 62 20 7 32 ->- 1000 42 Bjugn 63 48 9 40 1-' 110 0 43 Momyr 64 5 10 31 1930 44 Mære 63 54 11 31 760 45 Aursunden 62 41 11 28 740 Nordland 50 Susendal 65 22 14 15 620 51 Trofors 65 32 13 25 "•• 1400 52 Sandnes sjøen 66 1 12 37 1320 53 Vassvatnet 66 23 13 12 2760 54 Rognan 67 5 15 22 720 55 Rønvik 67 20 14 30 "- 1000 56 Kongsvatn 68 14 14 37 i 1600 57 Røst 67 30 12 4 700 58 Ankenes 68 23 17 17 780 F innmark 60 Kautokeino 69 1 23 2 320 61 Alta 69 58 23 15 310 62 Rypefjord 70 39 23 43 730 63 Mehamn 71 2 27 51 970 64 Høybukt 69 41 29 50 •v. 400 65 Øvre Pas- vik 69 10 29 12 •'- 3 50
Average values for th.e period 1900 - 1940 (11) . TABLE II
CONCENTRATION FACTORS RELATIVE TO HYLOCOHIUM SPLENDENS.
Weighed 0 S V MT N F average Physodes Pb 1.51 1.28 1.75 3.14 2.58 2.28 2.09 Cu 1.05 0.88 0.94 1.73 1.41 1.32 1.23 Zn 2.67 2.00 2.02 2.61 2.78 3.20 2.53 Cd 2.39 2.05 2.69 4.77 4.24 3.97 3.38
Cladonia Pb 0.35 0. 30 0.42 0.43 0.36 0.51 0.39 Cu 0.52 0.34 0.51 0.56 0.49 0.45 0.48 Zn 0.61 0.61 0.60 0.61 0.70 0.57 0.62 Cd 0.52 0.56 0.68 0.64 0.76 0.64 0.64
Sphagnum Pb 0.66 0.66 0.82 1.01 0.77 0.64 0.74 Cu 0.71 0.66 0.75 0.71 0.57 0.63 0.67 Zn 0.75 0.92 0.76 0.57 0.71 0.66 0.73 Cd 0.93 1.13 0.88 0.95 0.87 0.71 0.93 V 0.78 0. 64 0. 68 0. 74 0.82 - 0.74
Individual regions:
0 Østlandet S Sørlandet v Vestlandet MT Møre and Trøndelag N: Nordland F: Finnmark TABLE III DIFFERENCES IN TRACE ELEMENT LEVELS IN PLACES WITH HIGH(H) AND LOW (L) ATMOSPHERIC DEPOSITION, DEMONSTRATED BY MEANS OF DIFFERENT SPECIES
Pb Cu Zn Cd Physodes H 133 8.3 143 1.29 L 18.5 4.6 70 0.39 H/L 7.2 1.8 2.0 3.3
Cladonxa H 37 3.7 4 3 0.32 L 4. 0 2.1 14.2 0.064 H/L 9.3 1.8 3.0 5.0
Hylocomium H 108 10.2 72 0.68 L 8.4 3.9 26 0.094 H/L 12.9 2.6 2.8 7.2
Sphagnum H 69 5.9 64 0.75 L 8.2 3.5 13.5 0.084 H/L 8.4 1.7 4.7 8.9
11: Average of values from sampling sites nos. 20, 21, 23, 26, and 31 (ppm).
L: Average of values from sampling sites nos. 13, 41, 44, 50, and 61 (p^m). TABLE IV
CONCENTRATIONS OF 27 ELEMENTS IN SAMPLES OF HYLOCOMIUM SPLENDEMS FROM DIFFERENT PARTS OF NORWAY (PPM)
Sample no. Na
10 113 3090 10.3 0.18 0.08 0.27 0.0 3 0.07 2.4 2 . 2 11 83 3910 11.3 0. 14 0.07 0.20 0.03 0.06 3.9 1.6 12vl 166 2290 7.0 0. 07 0.12 0.34 0.04 0.09 2.0 1.4 13X) 402 3140 4.4 0.11 0.35 0.6 4 0. 09 0.14 4.0 3.3 14 221 3720 20.0 0. 60 0. 14 0.52 0. 09 0. 13 2.1 1.4 15 169 3660 25.9 0. 78 0.14 0.41 0.07 0. 15 2.4 1.9 16 128 3520 15.4 1.10 0.11 0.40 0.06 0.10 3.7 2.2 20 30) 3920 11.3 0.55 0.19 0. 50 0.07 0.14 7.9 4.2 21 155 4000 23.4 1.0 3 0.17 0.53 0.08 0.13 10. 1 3.8 22 260 3200 7.6 0.60 0 . 18 0.58 0.0 9 0.12 8.6 3. 3 23 232 3600 22.6 0.96 0.1S 0.68 0.11 0.18 6.4 3.8 24 194 3040 12.4 0.50 0.17 0.63 0.09 0.18 7.2 3.4 25 321 3310 5.7 0.24 0.19 0.49 0.08 0.14 8.4 3.5 26 175 2 390 8.7 0.33 0.16 0. 52 0.09 0.16 7.9 3. 1 30 500 3670 4.0 0. 10 0.10 0.45 0.06 0.09 2.7 1.6 31 159 2 640 7.9 0.5 7 0.12 0. 39 0.07 0.09 7.9 2.4 32 239 2860 7.4 0.21 0.08 0.2 3 0.04 0.0 6 3.6 5.2 4 8 0 3070 3.3 0.19 0.20 0.42 0.08 0. 10 5.9 3.6 )!*> 241 2640 j.4 0.13 0.18 1.15 0.11 0.03 2.1 1.6 3D 291 2450 6.7 0.14 0.11 0. 44 0 . 0 6 0.08 2. 3 1 .9 3D 464 3010 6.8 0. 13 0.11 0. 42 0. 06 0.0 8 4.8 1.3 37 322 3010 8.0 0.10 0.10 0.47 0.06 0.]3 2. 3 1. 2 40-> 172 2910 4.8 0. 10 0.08 0.33 0.04 0.0 4 1.7 0.7 41'° 273 3300 12.0 0. 28 0.19 0.55 0.09 0.13 0.9 1.7 42 297 2870 5.7 0.09 0.13 0. 28 0.04 0.07 2. 3 1.0 43 275 2190 3.3 0. 14 0.15 0.24 0.04 0.05 4.2 I. i 44 434 2630 9.6 0.11 0.15 0.33 0.05 0.10 1. 7 1. 1 45 1 10 3430 19. 1 0.36 0.0 7 0.12 0.02 0 . 05 0. 4 0.8 50 125 3020 9.1 0. 09 0.03 0.08 0.01 0.01 0. 9 0. J 51 258 3290 9.2 0. 15 0. 10 0. 19 0.03 0. 05 1.5 0.8 52 361 2120 4.6 0. 18 0.17 0.29 0.04 0.06 2. 1 1.2 53 271 2690 4.4 0.10 0.14 0.44 0.05 0.07 2.8 1.2 54 323 2830 11.8 0.23 0. 10 0.27 0.04 0.07 1 .9 0.8 5 5 379 3190 13.7 1.21 0. 18 0.46 0.06 0.11 2.0 1.7 56 553 2590 2.9 0.08 0.19 0.99 0.16 0. 11 3. 3 1. 2 57 4 97 1840 1.1 0.06 0.06 0.12 0.0 2 0.0 5 2. 2 0.7 58 268 2500 6.2 0.15 0.17 0.79 0.11 0. ]8 3.0 1.2 60X> 1900 3080 12.3 0.12 1.07 1.41 0.27 0.37 9. 2 8. 3 61 286 2640 4.8 0.08 0.10 0.20 0.02 0.05 0.8 1.1 62 339 2240 3. 7 0.12 0.19 1.03 0. 14 0. 11 2. 9 2.1 63 315 1710 1 .9 0.04 0.08 1.51 0. 27 0.05 1.2 0.8 64 302 2490 5.4 0.10 0.17 0.38 0.05 0.07 3.3 2.3 6 5 279 2040 7.5 0.09 0.21 0.41 0.06 0.0 7 0.3 2.8 x) The results indicate that the sample was to some extent con(aminated with soil material- 2
Sample no. Mo U Mn Fe Co Cu Ag Zn 10 u.12 - 0.03 340 400 0.18 5.0 0.08 41 11 0.10 0.03 220 310 0.16 5.5 0.11 38 12 s 0.10 0.04 260 380 0.19 3.1 0.05 40 13X' 0.10 > 0.03 290 1230 0.56 3.3 0.02 24 14 - 0.10 0.07 240 630 0.29 4.9 0.0 f- 35 15 0.10 0.04 340 500 0.25 5.1 0.16 53 16 0.15 0.06 240 550 0.37 5.9 0.09 61 20 0.39 0.09 140 680 0.48 9.1 0.19 67 21 0.35 0.09 380 750 0.40 11.9 0.26 80 22 0.27 0.12 210 800 1.16 28.8 0.59 70 23 0.31 0.10 340 750 0.51 10.4 0.23 69 24 0.12 0.12 120 770 0.33 9.1 0'. 45 5b 25 0.29 0.06 210 710 0.35 9.8 0.16 48 26 0.35 0.08 80 740 0.34 10.5 0.24 71 30 0.22 0.11 90 510 0.24 5.3 0.10 50 31 0.44 0.08 80 550 0.24 9.2 0.30 74 3 2 0.12 0.08 110 370 0.22 5.3 0.04 49 33 0.42 0.08 150 740 0.27 4.6 0.07 30 34x) 0.10 •- 0.03 290 1650 1.24 4.4 0.08 32 35 • 0.10 0.04 140 340 0.18 4.2 0.05 41 36 0.16 - 0.03 160 410 0.27 5.9 0.17 58 37 • 0.10 0.04 90 360 0.18 3.1 0.04 28 40, 0.14 •• 0.03 200 350 0.15 3.5 0.07 21 41*' • 0.10 0.0 3 140 690 0.31 4.5 0.03 23 42 0.18 •. 0.03 260 380 0.16 3.8 0.10 25 43 0.16 -• 0.03 430 430 0.21 6.1 0.03 34 44 '0.10 0.04 130 540 0.28 3.4 0.04 29 45 0.10 0.06 440 260 0.23 4.1 0.03 46 50 - 0.10 0.03 690 130 0.67 2.8 0.06 35 51 -CIO '0.03 220 380 0.15 2.9 0.03 27 52 0.10 0.05 160 450 0.19 2.6 0.08 19 53 -0.10 0.04 110 630 0.18 5.2 0.19 40 54 0.10 •' 0.03 300 410 0.30 3.8 0.02 35 55 • 0.10 0.12 60 790 0.23 5.6 0.13 18 56 '0.10 -0.03 100 730 0.20 6.3 0.06 33 5 7 0.10 0.0 3 30 210 0.09 4.5 0.14 11 58 -0.10 0.06 230 1540 0.35 4.3 0.05 31 60*' . 0.10 0.14 720 3700 1.57 9.1 0.20 34 61 • 0.10 - 0.03 410 410 0.41 5.4 0.04 18 62 - 0.10 0.05 30 680 0.97 5.3 0.07 18 6 3 0.12 0.11 50 300 0.37 4.0 0.10 35 64 0.10 0.03 380 400 1.12 19.4 0.09 28 6 5 - 0.10 0.04 500 950 0.90 12.6 0.07 27
The results indicate that the sample was to some extent contaminated with soil material. 3
Sample no. Cd Hg Al Pb AS Sb Se Cl Br
10 0.26 0.07 140 39 0.81 0.35 0.29 90 3.6 11 0.25 0.05 110 35 0.42 0.22 0.19 40 2.9
12 16.4 0.13 vl 0.24 0.05 300 0.17 0.12 60 1.6 13x) 0.09 0.11 630 8.3 0.25 0.07 0.08 110 2.2 14 0.17 0.13 440 30 0.26 0.12 0.10 90 3.2 15 0.37 0.11 150 49 0. 52 0. 36 0.36 90 3.6 16 0.62 0.14 170 43 0.67 0.36 0.24 150 4.8 20 0.55 0.15 240 83 1.06 0.77 0.59 240 7.8 21 0.82 0.20 290 148 1.59 0.87 0.88 2 50 6.7 22 0.64 0.12 310 101 1.91 0.92 1.09 250 8.2 23 0.70 0.16 200 97 2.33 0.89 0.90 180 8.7 24 0.59 0.18 310 82 1.35 0.81 0.71 200 7.9 25 0.42 0.17 370 85 1.04 0.79 0.80 300 10.8 26 0.86 0.13 260 115 1.43 0.94 l.oe 150 9.9 30 0. 39 0.12 370 43 0.48 0.29 0.40 390 12.8 31 0.4b 0.16 340 99 1.06 0.70 1.00 110 10.9 32 0. 39 0.09 140 39 0.86 0.31 0.42 244 18.0 33 . 0.31 0.16 250 30 0.73 0.46 0.55 370 ia. 7 34X) 0.29 0.11 530 12.1 0.15 0.11 0.12 190 3.6 35 0. 12 0.09 350 27 0.28 0.15 0.14 70 8.3 36 0. 58 0.13 270 42 0.35 0.24 0.51 120 9.3 37 0. 14 0.09 180 14. 0 0.25 0.12 0.18 60 5.7
40 0. 15 0.06 15.0 0.13 0.07 0.11 130 xl 180 5.6 41X' 0 . 07 0.05 370 9.2 0.13 0.09 0.05 100 3.9 42 0.15 0.09 230 24 0.23 0.13 0.29 50 7.6 43 0.17 0.08 560 20 0.27 0.10 0.39 170 8.3 44 0.09 0.12 340 10.2 0.23 0.09 0.22 200 9.4 45 0.18 0.11 140 7.2 0.14 0.06 0.11 170 3.9 50 0.13 0.11 30 6.0 0.15 0.05 0.08 240 4.6 51 0.09 0.11 220 13.5 0.21 0.05 0.20 110 fi. 5 52 0.13 0.17 310 23 0.23 0.12 0.36 220 7.7 53 0.39 0.14 130 52 0.39 0.25 0.81 360 10.3 54 0.11 0.08 300 12.7 0.31 0.08 0.2£ 190 7.1 55 0.15 0.08 160 16.2 0.18 0.10 0.28 220 9.4 56 0. 30 0.15 390 42 0.33 0.19 0.93 200 13.2 57 0.10 0.12 130 15.6 0.58 0.12 0.42 410 15.9 58 0. 14 0.07 320 14.0 0.29 0.11 0.19 100 3.4 60x) 0.12 0.11 2170 12.6 0.32 0.10 0.12 90 2.2 61 0. 09 0.08 250 8.1 0.24 0.07 0.13 90 4.0 62 0. 12 0.14 310 15.9 0.24 0.11 0.29 180 10.1 63 0.29 0.16 150 12.0 0.23 0. "Ml 0.30 130 12.4 64 0. 18 0.06 510 19.1 0.69 0.16 0.23 180 2.9 65 0.13 0.14 290 10.4 0.81 0.12 0.25 60 3.1 Sorla«Jet
F'ig. 1. Location of sampling sites Jf • ^WP
i rfa-
Fig. 2. Regional distribution of vanadium (ppm) itA&J
Fig. Regional distribution of copper (ppm) Fig. 4. Regional distribution of zinc (ppm) ..^Æ
c.og a.2t
Fig. 5. Regional distribution of cadmium (ppm) Fig. Ci. Regional distribution of lead (ppm} Fig. 7. Regional distribution of antimony (ppm) ^* 0.31 ,
Fig. 8. Regional distribution of arsenic (ppm) Fig. 9. Regional distribution of selenium (ppm) Fig. 10. Regional distribution of bromine (ppm)