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STUK-A62

June 1987

RADIOACTIVITY OF GAME MEAT IN AFTER THE CHERNOBYL ACCIDENT IN 1986

Supplement 7 to Annua! Report STUK A55

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STV K - A - - 6 2. . STUK-A62

June 1987

RADIOACTIVITY OF GAME MEAT IN FINLAND AFTER THE CHERNOBYL ACCIDENT IN 1986

Supplement 7 to Annual Report STUK-A55

Aino Rantavaara, Tuire Nygr6n*, Kaarlo Nygren* and Tapani Hyvönen

* Finnish Game and Fisheries Research Institute Ahvenjärvi Game Research Station SF - 82950 Kuikkalampi Finnish Centre for Radiation and Nuclear Safety P.O.Box 268, SF-00101 FINLAND ISBN 951-47-0493-2 ISSN 0781-1705

VAPK Kampin Helsinki 1988 3

ABSTRACT

Radioactive substances in game meat were studied in summer and early autumn 1986 by the Finnish Centre for Radiation and Nuclear Safety in cooperation with the Finnish Game and Fisheries Research Institute. The concentrations of radioactive cesium and other gamma-emitting nuclides were determined on meat of moose8 and other cervids and also on small game in various parts of the country before or in the beginning of the hunting season.

The most important radionuclides found in the samples were 134Cs and 137Cs. In addition to these, 131I was detected in the first moose meat samples in the spring, and 110"Ag in a part of the waterfowl samples. None of them was significant as far as the dietary intake of radionuclides is concerned.

The transfer of fallout radiocesium to game meat was most efficient in the case of the arctic hare and inland waterfowl; terrestrial game birds and the brown hare belonged to the same category as moose.

The nationwide mean contents of radiocesium in different types of game meat, weighted for areal distribution of both the annual game bag and deposited radiocesium, are given below together a The scientific and Finnish names of the species are given in Table I. 4 with the mean dietary intakes via game meat:

Type of game Content (Bq kg "; ) Intake (Bq per person) meat i3*Cs I37Cs "« Cs "7 Cs

Moose 80 170 77 194 Cervids other than moose 190 400 11 28 Hares 200 420 14 35 Waterfowl 150 310 12 25 Terrestrial game birds 50 130 2 5

Intake in 1986 47 106 Intake in 1987 69 180 Total intake via game meat 1986.'1987 120 290

The contribution of cervids to the total dietary intake of radiocesium via game meat was 3/4, which was slightly less than their contribution to the annual game bag.

On the basis of the preliminary results of this study it was concluded in autumn 1986 that there was no need to restrict hunting in the year 1986/1987.

The radiocesium found in the .neet of terrestrial game animals did not necessitate any recommendations on their use. As regards the meat of waterfowl caught in the main inland fallout area, it was recommended not to eat more than 20 kg per person. 5

CONTENTS

ABSTRACT

CONTENTS

INTRODUCTION 7

MATERIAL AND METHODS 2.1 Sampling 9 2.2 R-rdionuclide analysis 10 2.3 Data treatment 2.3.1 Estimation of transfer factors 11 2.3.2 Estimation of areal radiocesium contents 12 2.3.3 Estimation of dietary intake 13

RESULTS 3.1 Radionuclide contents of game meat 15 3.2 Transfer of fallout radiocesium to game meat 16 3.3 Dietary intake of radionuclides via game meat 16

DISCUSSION 4.1 Radionuclide contents of game meat 18 4.2 Transfer of radiocesium to game meat 4.2.1 Game meat in general 19 4.2.2 Moose and other cervids 21 4.2.3 Small game 22 6

4.3 Dietary intake of radiocesium

via game meat 23

5 ACKNOWLEDGEMENTS 25

REFERENCES 26

FIGURES 29

TABLES 40 7

1 INTRODUCTION

The survey of radioactive substances in game meat in 1986 was a part of the fairly comprehensive monitoring of foodstuffs carried out by the Finnish Centre for Radiation and Nuclear Safety (STUK). The objective was to determine the degree of contamination of game meat by the radioactive fallout of spring 1936, in order to assess the importance of game meat as a dietary source of radiocesium. Information on the environmental transfer of radiocesium through natural food chains was also obtained. The Finnish Game and Fisheries Research Institute was responsible for the organization of sampling and gave biological expertise at different stages of the study.

Moose*, also called elk, is by far the most important game animal in Finland, with a winter population of 78 000 - 85 000 individuals in 1985 - 1987, and almost 45 000 - 55 000 animals culled annually.8 Moose was also the species for which the present sampling was most representative. The next most important species in the group of cervids, to which it belongs, is the white-tailed deer. About 86 % of the annual game bag of 9 x 106 kg in Finland came from this group of animals. Hares and waterfowl contributed most to the annual small-game bag in 1986/1987. Altogether, game meat added about three per cent to the average 66 kg per capita consumption of meat produced by animal husbandry.

Hunting is to some extent concentrated in southern and central Finland,3 where the deposition of radioactive substances was higher than in the northern and easternmost parts of the country. When the mean deposition of 13 7 Cs was weighted for the areai game bag, the nationwide mean, 14 kBq 137Cs per square meter, exceeded the surface area weighted mean for Finland by a factor of I.3.1

The radioactive fallout of spring 1986 arrived in Finland at a time when a gradual, for some terrestrial species radical, change

• The scientific and Finnish names of the species are given in Table I, 8 in forage was beginning, in connection with the snow melt. At this time, too, moose were migrating to summer pastures. The maximum intake of radionuclides by game animals occurred immediately after the arrival of fallout, via forage plants exposed directly to deposition of radioactive substances. The intake of radio-nuclides by terrestrial game animals decreased in summer, when fresh grass and leaves of trees not exposed directly to fallout became available.

The transfer of radiocesium from fallout to meat is more efficient in natural food-chains than in animal husbandry. This was evident in a previous study on radiocesium in moose meat in Finland. The study from 1979, made when annual deposition of 137Cs was low, revealed large ranges of 137Cs contents in areas with the same or comparable accumulated deposition. Some sources of the variation were identified, as for example forage plants with high mineral contents, growing on wetlands, and mushrooms in autumn.10

The same factors as earlier affected the radiocesium contents of game meat in 1986, additional pathways being direct deposition on forage plants in the spring and contamination of drinking water by fallout. The probably efficient transfer of radiocesium from the new fallout to game meat and the large ranges that could be expected in the radiocesium contents prompted us to assess the contamination before the hunting season of 1986. At the beginning of autumn 1986, the only important nuclides were 134 Cs and 137Cs. 9

2 MATERIAL AND METHODS

2.1 Sampling

When the sampling programme wa» planned, areal differences in the deposited amounts of radiocesium were not known in detail (Fig. 1). To fulfil the requirement of advance information to consumers of game meat, nationwide sampling seemed necessary for at least the most important game animal, moose.

Samples were taken of altogether 16 species, of which 15 belong to those hunted in Finland. Only a few species were chosen as the main representatives of groups of birds living in similar environments or using the same type of food. The numbers of samples were roughly proportioned to accord with the contributions of different species or groups to the annual game bag:

Group or species Number of samples

Moose 298 Cervids other than moose 34 Hares 23 Waterfowl 79 Terrestrial birds 15

The majority of the samples were taken before the hunting season. By order of the Ministry of Agriculture and Forestry, the police districts provided samples of moose and white-tailed deer killed or Injured in traffic accidents. The Game and Fisheries Research Institute conducted experimental hunts, which supplemented the moose samples and provided most of the samples of small game. The Northern Research Station of STUK delivered moose samples from . Many private persons and local Game Management Associations also assisted in sampling. 10

The samples for the study were collected from the whole country (Figs. 2 - 7), except for small game, which In Lapland was studied by the Northern Research Station of STUK.13 The sampling locations of moose represented 163 municipalities.

The samples of moose meat were usually taken between the shoulder blades or from the neck. About half a kilogram of chilled moose meat was sent by express delivery to the laboratory, with records of the location and date of sampling, and the sex and age group (adult/calf) of the animal. Samples of small game were often sent as whole animals. These were cleaned and a sample was taken of the breast muscle In the case of birds, and the hind leg In the case of hares.

2.2 Radionuclide analysis

All the samples were analysed for gamma-emitting fallout nuclides, most of them as individual samples. In a few cases two or more samples from nearby locations were combined. The total number of gammaspectrometric analyses of moose meat was 274 and that of other game 124. visible fat and connective tissues were removed from the samples before analysis. Normally, samples were measured fresh, except those from North Finland, which were first dried at 105 °C and homogenized.

The gamma emitting nuclides in the samples were measured using low-background semiconductor spectrometers. The relative efficiencies of the lithium-drifted or high-purity germanium detectors varied between 15 and 39 per cent. The gamma spectra were analysed with a computer program GAMMA-83, which has been developed by STUK for environmental sample analysis.16 Corrections for both density and volume of the sample and the true coincidence summing correction were included in the programmme.17 11

Three different sample geometries, two cylindrical and one of the Marinelli type, were used, depending on the volume of the sample. The detection limit for both 137Cs and 134Cs was about 1 Bq kg'1 . The relative standard deviation of the determination of radiocesium usually varied between 1 and 10 per cent, being most often under 5 per cent. For short-lived, occasicnally detected radionuclides the detection limit varied.

2.3 Data treatment

2.3.1 Estimation of transfer factors

In order to obtain reliable estimates for the mean radiocesium contents of different types of game meat and for the dietary intake of radiocesium, areal differences in the fallout had to be taken into account. This was done by first calculating the fractions of deposited radiocesium which had been transferred to individual meat samples from different locations.1 Estimation of radiocesium contents from areal deposition data was necessary for species the sample numbers of which were small. It also improved the accuracy of nationwide or areal assessments for other species included in the programme. The division or Finland into 15 game management districts and the province of Aland was the basis for the areal treatment of the data (Fig. 2).

The average deposition? of 137Cs from the Chernobyl fallout given for the Finnish municipalities were used in calculating the weighted mean depositions for different game management districts and nationwide. These data were also used, when the factor describing the transfer of radiocesium from fallout to individual game meat samples was calculated.1

The part of the radiocesium originating from the Chernobyl fallout was estimated with 134Cs, which did not occur in the previous fallout from atmospheric nuclear weapons tests. The constant ratio of the 134Cs and 137Cs contents in the new fallout, 0.52 on 1 October 1986, was used when amounts of either 12 of the nuclides had to be converted to those of the other nuclide.1

The fraction of the new radloceslum deposited ^r unit area that was transferred to game meat was given as the ratio TF, called here the transfer factor (equation 1). For calculation of TF only such samples were chosen in which 134Cs was detected.

... __ 134 Cs or 137Cs in a meat sample (Bq kg'1 ) Mean 134Cs or 137Cs deposition in the sampling municipality (Bq m~2 )

2.3.2 Estimation of areal radiocesrium contents

13 7 The surface area-weighted mean deposition of Cs (D± ) in a game management district (i), and the mean content in meat of 13 7 Cs originating from the fallout of previous years (AQ) were used 137 in estimating the areal mean contents of Cs (At ) for a species:

(2) At = Ao + D± x TF

134 When AA was estimated for Cs using equation 2, AQ was zero

and the .nean deposition D± was multiplied by 0.52.

The mean content of the old 137Cs, AQ , used for the meat of a species or group of animals was the same for the whole country, since a previous study had shown that the areal mean contents in moose meat did not differ significantly.10

For species studied in 1986 by the Northern Research Station cf STUK, and not sampled representatively for the present study, the data from Lapland were included in the material from which

A0 and TF were calculated. These species were the willow grouse, capercaillie, hazel hen, goosander and arctic hare.13

In estimating both A0 and TF to be used in equation 2, the moose samples were divided into calves and adults, the age li.nit being 13 one year. Due to the decreasing trend in the transfer factors for moose in the spring, the values for TF were based on samples taken after 20 June.

Waterfowl from coastal areas or archipelagoes and those from inland environments were treated as separate groups. The minimum

values of both A0 and TF were chosen for estimating the radiocesium contents in coastal waterfowl.

The nationwide mean content of radiocesium in the meat of a species, weighted for annual catches. A,,,, , was calculated as follows:

1 (3) A,. = (ENi)" S N,. At , ±•1 i-l

where N< = Annual catch of a species in a game management district (i), given as the number of individuals.

The annual catches were available for more than 20 of the most important game animal species. The statistics for the hunting year 1986/1987 were used.4-619

The division of the annual catches of waterfowl into those of inland and coastal origin was based on both species-specific and areal information as regards mainly marine populations.5-12 The proportion of a 20-km-broad coastal zone in the areas of the different game districts was used in estimating the proportions of inland and coastal birds in catches of other than purely marine species of waterfowl.2

2.3.3 Estimation of dietary intake

The dietary intake of radiocesium through human consumption of different species (I) was estimated using the catch statistics, the average carcass weights (m) of different game animals, and 14 the areal or nationwide mean contents of radiocesium for a species or a group of game animals (equations 4 and 5). Carcass weight means weight of the whole animal except for head, legs below knees, entrails and skin. For estimation of the weight of edible meat, a correction factor (k) was used for the proportion of bone weight in equations 4 and 5.

(4) Ii = k m Ni A±

16 (5) I„ «kKJ NjlxA. i-1

The values of k were the following:18

moose, adult 0.80 moose, calf 0.78 other cervids 0.78 hares 0.90 birds 0.90.

The total dietary intake of radiocesium via game meat was the sum of the intakes via individual species hunted in the year 1986/1987.

Radioactive decay was taken into account in the intake estimates. The consumption periods observed were September - December 1986 and January - July 1987, and the activities were corrected to the date in the middle of each period. Birds were assumed to be consumed during the first period, whereas the intake of radionuclides via cervids and hares continued on an average up to the end of July 1987. The sample-specific contents w^re given corrected to the date of sampling, whereas in areal comparisons of contents the reference date for all contents was 1 October 1986. 15

3 RESULTS

3.1 Radionuclide contents of gaae meat

The radiocesium contents of individual meat samples, grouped by species and game management district (Tables II - VI), were the basis for the transfer factors, which were used in calculation of areal and nationwide means (Table VIII, Figs. 10 - 12).

The arithmetic means of the radiocesium contents measured in moose meat samples from each of the five fallout areas show dependence on deposited radiocesium (Fig. 8).

Areal and nationwide mean contents of radiocesium were calculated for five groups of species of game animals, using equations 2 and 3 (Fig. 9). Finland was divided according to deposited radiocesium into a nain fallout area and an area of minor deposition. The second area included the game management districts of North , , and Lapland and the province of Aland, and the first area all the other districts. The mean radiocesium contents in moose meat, weighted for areal deposition and catches, were:

134 Cg 137Cg

Whole country 80 170 Bq kg"1 Main fallout area 130 270 " " Area of minor deposition 10 40 " "

The weighted concentrations of radiocesium in meat of cervids other than moose in the main fallout area were somewhat higher than the contents in moose meat, but still of the same order of magnitude. In the main fallout area, inland waterfowl and arctic hare clearly contained more radiocesium per kilogram than other game. Terrestrial game birds and the brown hare had the same level of radiocesium contents as moose (Fig. 9). The nationwide mean contents were: 16

13«Cs 137Cs

Cervids other than moose 190 400 Bq kg"1 Arctic har°e 210 450 Brown hare 110 220 Waterfowl inland 210 430 coastal 10 30 Terrestrial game birds 50 130

In addition to radionuclides of cesium, 110"Ag was found in water birds caught in some of the municipalities of the highest fallout categories (Fig. 1, Table V). 131I was found in all moose meat samples taken in May or early June. The contents in these samples which represented locations belonging to different fallout categories varied between 8 and 230 Bq kg'1 . Occasionally also i29mrf,e an(j i3 2»re were found in moose samples of the spring and summer (Table VII).

3.2 Transfer of fallout radiocesium to game meat

The arithmetic means, medians and ranges of the transfer factor, TF, for moose and other game (Table VIII, Fig. 11), describe the transfer of radiocesium from the environment to the meat of different game animals. The frequency distribution of TF for adult moose was approximated using a gamma distribution, a = 2 and @ = 0.005 as parameters. The distribution gives the 95 % confidence limits 0.0012 < TF < 0.030 m2 kg"1 for the transfer factor (Fig. 12).

3.3 Dietary intake of radionuclides via game meat

When the total game bag of the hunting year 1986/1987 was taken into account, the per capita intake of 134 Cs via game meat for the whole population of Finland was 120 Bq and that of 137Cs 290 Bq. Game moat is usually mainly consumed by the hunters' 17 households - approximately 500 000 people. When the dietary intake of radiocesium via game meat was divided between the probable intake periods in 1986 and 1987, the average per capita intakes for the whole population of Finland and for the hunters' households, given in Bg per person, were:

Whole population Hunters' households

13«Cs 1986 50 470 1987 70 680 137Cs 1986 110 1000 1987 180 1800

Cervids contributed about three quarters (77 %) of the dietary intake of radiocesium via game meat. This was slightly less than their contribution to the annual game bag (86 %). The next most important groups as regards intake of radiocesium were hares and waterfowl (Fig. 14).

The contribution of different game districts to the total dietary intake of radiocesium varied, depending on the fallout and on the importance of different game animals. The highest contributions were those of the districts of Northern Häme and Central Finland; the lowest were in the districts of minor deposition, in Aland, in northern Finland and in . Almost all the dietary radiocesium originated from the main fallout area, although the contribution of this area to the annual game bag was not more than 60 % (Figs. 13, 14).

As regards the intake of radionuclides other than those of cesium, only 110»Ag was detectable when hunting began. It has a half-life of medium length, 250 days. The mean dietary intake during the period September - December 1986 was less than 2 Bq per person, when the consumption of waterfowl was divided among the whole population of Finland. 18

4 DISCUSSION

4.1 Radionuclide contents of game seat

The main results of this study are the areal and nationwide means for the radiocesium contents of and the intake via different types of game meat. These were estimated by weighting the location-specific results for the distributions of both radiocesium deposition and catches of game. For moose meat, however, the arichmetic means of the radiocesium contents for different game districts did not differ much from those obtained by weighting. Two of the districts, Ruotsalainen Pohjanmaa and Varsinais-Suomi, clearly show the necessity of using transfer factors in areal assessments (Table IX).

The nationwide mean contents of 137Cs in moose meat in autumn 1986 and in beef in May - December 1986 can be compared with those in 19791011 :

Moose meat Beef

1906 170 74 Bq kg-1 19?9 34 1.2

The contents differ due to differences in both the food and the animal species. These results confirm that the xadiocesium contents of cultivated forage plants are lower than those of natural forage in the case of fresh or old fallout accumulated in the soil. The two ruminants also differ in feeding strategy and in digestion.

The moose is a so-called concentrate selector,7 It uses selectively a variety of vascular plants from early summer onwards, consuming relatively large quantities of food. The annual nutrition of the moose has clear seasonal changes. The cow is a grass and roughage eater all through the year. The species also differ in the rate of flow of the ingesta, which varies widely with the season in the case of the mcose, but is constant in the case of the cow. 19

The sampling was carried out before the hunting season, but information was needed on the situation during the season. To judge the relevance of the study in this respect, the changes in intake of radionuclides by game animals after the arrival of fallout had to be considered. Besides this, the biological half-lives of radiocesium for the different species determine, how important the intake history was to the radiocesium contents in meat at the time of hunting.

The biological half-life of radiocesium in game animals varies, depending, among other things, on the size and metabolism of the species. For adult moose, the biological half-life is about one month, and for smaller animals it is shorter. For all game animals some or several half-lives had elapsed between the period of maximum intake and the start of hunting. Thus the contamination of meat had decreased from the highest values in the spring.

The contents of 131 I in moose meat in May and June (Table VII) indicate, that several times higher contents could have been found in all game meat in the beginning of May.

4.2 Transfer of radiocesium to game meat

4.2.1 Game meat in general

The transfer factor was used in order to eliminate the random effect of fallout differences on areal radiocesium contents, when sampling was not representative enough to give reliable arithmetic means. Actually, the quantity defined here as transfer factor (equation 1) gave values of a certain transfer function at the time of sampling.

Besides the characteristics of the locally deposited radiocesium, other factors affecting the transfer of radiocesium to game meat are the metabolism of the species, the age and size of 20 the individual, the type of food and via it the environment and the season.

The sources of variation and uncertainty in transfer factors are in principle the same as those for the radiocesium contents of the samples, together with those for the estimation of 137Cs deposition, as was discussed previously.111

The beginning cf winter migration of animals often coincides with the start of the hunting season, for example in some waterbirds and the moose. Thus the hunting location is not always the same as the environment in which the animals have lived in the previous weeks. Sampling in the living environment was essential, when the transfer factors were used to assess the degree o£ contamination of game meat by radiocesium as a whole. The timing of sampling in this study was ideal for minimizing the variation due to migration of the ammals. However, in environments of varying fallout radioactivity, our results were affected by both the normal daily migration of animals and the additional uncertainties connected with the estimation of mean radiocesium deposition in such municipalities (Fig. I).11

The information obtained on the transfer of radiocesium to the meat of different wild-life species in Finland was also uncertain for species for which the sample numbers were smallest. The best data were obtained for moose, but those for other game animals accorded well with the conditions prevailing during sampling. When TF values of the same order of magnitude are obtained for different species, this may be due to many different, sometimes opposite, factors. Agreement was also found, when foodstuffs of agricultural or aquatic origin were compared with game meat. In order to elucidate the species-specific transfer of radioceoium in different environments, more systematic surveys are needed. 21

4.2.2 Moose and other cervids

When the transfer factors calculated for moose meat are given as a function of sampling time (Fig. 10, 11, Table VIII), the figures for early summer can be seen to differ from the others. This can be explained by the exceptionally high contents of radionuclides in forage plants in spring, due to direct deposition on plants. The moose eats large amounts of forage at that time of the year when it is compensating for the poor winter nutrition, or, in the case of calves or young adults, needs food for growth. The higher than average transfer factors, found in spring for the moose indicate a high seasonal radiocesium intake, which did not occur later in the summer.

The normal early spring diet of the moose includes shoots of deciduous trees and pine. As the snow melts, the forage gradually changes to dwarf shrubs, the whortleberry being especially important. The intake of radionuclides decreased after early summer, when fresh vascular plants, not directly exposed to fallout, became available. In July the content of dietary fibre increases in the forage of the moose. This increases the part of the food which is digested by ruminating, and may thus affect the absorption of cesium from the digestive tract. Winter forage, for example pine twigs, gradually replaces fresh forage in the moose diet in autumn. This was not expected to cause a significant change in the intake of radiocesium by moose in 1986.

Exceptionally high transfer factors are possible for moose in autumn also, due to casual sources of radiocesium in the diet, for example mushrooms or plants growing on wetlands and rich in minerals.10 Animals with exceptionally high radiocesium body burdens can thus have occurred among the hunted moose.

As regards the age groups of moose, transfer of radiocesium to meat of calves was slightly more efficient than to meat of adults. The difference in size and metabolic activity of the animals may be partly responsible, but this is also due to their different diets. Calves receive part of the radiocesium in milk; 22 towards early autumn the proportion and quantity of forage increase in the diet. An additional source of radionuclides in the diet of calves is mineral soil, which the calves like to lick, especially in early summer. A tendency for the transfer factors to decline in the course of summer and early autumn was confirmed with the monthly means in the age groups of both adults and calves (Fig. 11).

The transfer of radiocesium to moose meat did not differ much between the years 1986 and 1979, when different fallout situations prevailed. The average transfer factors were 0.0097 (adults) and 0.015 (calves) in 1986 and 0.011 - 0.026 m2 kg1 for all ages in 1979. The cumulative deposition used for 1979 was an estimate of the nationwide mean, which did not take account of areal differences or the decrease due to runoff.14

More precise information on the transfer of radiocesium to moose will be obtained later from a fairly comprehensive study made by us during the hunting season of 1986. Radiocesium was determined on different soft tissue samples, which gave good representation of all the game management districts and were collected with systematic background information on the samples.

Transfer of radiocesium from fallout to the meat of white-tai led deer was only slightly more efficient than in moose, in spite of the small size of the species. Different forage plants and the greater tendency of the deer to frequent cultivated environments may be the reasons for the small difference between the two species.

4.2.3 Small game

The transfer factors for hares revealed a clear difference in the intakes of radiocesium by arctic and brown hares. The arctic hare is somewhat smaller than the brown hare, but this can only partly explain why the transfer to the meat of the arctic hare is about three times as high. The arctic hare favours forest surroundings with sparse vegetation, whereas the brown hare 23 has adapted to living in Finland by choosing denser field vegetation, where soil-to-plant transfer of radiocesium is markedly smaller than in the environments of the arctic hare. This can cause differences in the radiocesium contents of the forage, and thus a smaller intake of radiocesium by the brown hare.

Special interest attached to waterfowl, since their food is of aquatic origin. For the species feeding on the bottom fauna or fish, in particular, the radioactivity of their food increased as the season advanced. The transfer factors obtained for coastal areas were approximately one order of magnitude lower than for inland environments. Only a few of the sampling locations lay in coastal municipalities. Part of the samples were taken in the beginning of the hunting season, which often coincides with migration of waterbirds to locations rather far from their summer environments. Migration from the coast to inland waters is also possible. The minimum transfer factors obtained for waterfowl, regardless of the sampling location, were used in estimating the radiocesium contents for birds belonging to marine food- chains. The possible difference in deposition of radiocesium in the original environment and the hunting municipality was disregarded here, as the contribution of marine waterfowl to the total dietary intake of radiocesium was of minor importance.

Samples of several species of small game taken from the same or nearby locations were also studied. Such sets of samples most often confirmed the degree of environmental transfer typical of a certain environment. Sampling location showing this was, for example, in the district of Southern Häme.

4.3 Dietary intake of radiocesiua via game meat

Game meat made a smaller contribution to the average dietary intace of 137Cs in the hunting year 1986/1987 (2 %) than in the year 1979/1980 (15 %), which is here taken as representing a period of low annual deposition of i37cs:10n15 24

137Cs received during 1986/87 1979/80 12 months via

Game meat 290 65 Bq per person Meat excluding game 2400 40 Total diet 12000" 450 a Estimate for May 1986 - April 1987.

Unlike other foodstuffs, game meat is largely consumed in the hunting areas. The intake of radiocesium via game meat in different districts varied by a factor of 0.2 - 3 around the nationwide mean, when per capita consumption was assumed to be the same (Fig. 13).

Jn view of the preliminary results of this study, and on the recommendation of the Finnish Centre for Radiation and Nuclear Safety, the Ministry of Agriculture and Forestry decided that there was no reason to restrict hunting in autumn 1986. Meat of moose and other cervids could be used as before throughout the country. It was recommended that the consumption of waterfowl caught in the main inland fallout area in the hunting season of 1986 should be limited to 20 kg per person. Other small game could be used as before throughout the country.9

After a more comprehensive analysis of the results, and taking the large annual catches of hare into account it can be concluded that the next most important game animal to have been included in the recommendation mentioned above, would have been the arctic hare. 25

5 ACKNOWLEDGEMENTS

The authors wish to thank all the persons who assisted in sampling, especially Mr Matti K. Pirkola, M.Se, and Mr Heikki Koivunen from Finnish Game and Fisheries Research Institute for conducting the experimental hunts of small game, and Mr Ilkka Ala-Ajos and Mr Heikki Vakkuri from the Hunters' Central Organization, Mr Petri Nygren, Mr Tom Tötterman, Mr Kauko Saarni and Mr Pekka Lajunen for voluntarily assisting in experimental hunls of moose and Mr Rolf Vennström, the Provincial Vet., for delivering samples from the province of Aland. We also want to thank the personnel of the police districts, the Ministry of Agriculture and Forestry, the Haapasaari coastguard and the Game Management Associations of -Tammela, , , Lehtimäki-Soini, Lohtaja, -, and Ähtäri.

We are very grateful to Mr. Aslak Ermala, Dr. Eero Helle and Dr. Hannu Pöysä of the Finnish Game and Fisheries Research Insti­ tute, for discussions on Finnish populations of small game and on the behaviour of different species, and to Mr Mauri Pesonen, B.Sc, from the same institute, forgiving statistical expertise.

Our thanks are due to the personnel of the Laboratory for Radionuclide Monitoring for their helpful attitude during the busy times of the study.

We are also indebted to the Acting Director of the Surveillance Department, Olli Paakkola, and to the Acting Head of the Laboratory for Radionuclide Monitoring, Matti Suomela, for their valuable comments during the work. 26

6 REFERENCES

1 Arvela H, Blomqvist L, Lemmelä H, Savolainen A-L, Sarkkula S. Environmental gamma radiation measurements in Finland and the influence of meteorological conditions after the Chernobyl accident in 1986. Report STUK-A 65. Supplement 10 to ^nual Report STUK-A55. Helsinki: Finnish Centre for Radiation and Nuclear Safety, 1987.

2 Ermala A. The Finnish Game and Fisheries Research Insti­ tute, Helsinki. Personal communication.

3 Ermala A. In Proceedings of the XVIII Congress of the International Union of Game Biologists. Poland 1987. (To be printed.)

4 Ermala A. Metsästysvuoden 1986/87 pienriistasaalis. Riistantutkimusosaston monistettu tiedote No 74. Helsinki: Riista- ja kalatalouden tutkimuslaitos, 1988. (In Finnish.)

5 Harberg J. Landskapsstyrelsen Aland. Personal Communication

6 Niemelä E. Viime syksyn hirvijahdin tulos. Metsästäjä 1987; 1: 12 - 13. (In Finnish.)

7 Nygren K, Hofmann RR. Sei selektiv und bleib am Leben! Morphophysiologische und ethologische Anpassung an die jahreszeitlich wechselnde Äsungsverfiigbarkeit beim europäischen Elch, Alces alces, in der nördlichen Taiga. Jagdwissenschaft und Wildbiologie 1987; 5: 3-5.

8 Nygren T. Riistantutkimusosaston monistettu tiedote No 47. Helsinki: Piistä-ja kalatalouden tutkimuslaitos, 1986. (In Finnish.) 27

9 Radioactivity of game meat in Finland. Bulletin 16 September 1986. Helsinki: Finnish Centre for Radiation and Nuclear Safety, 1986.

10 Rantavaara A. Caesium-137 in moose meat in Finland. Suomen Riista 1982; 29: 5 - 13. (In Finnish, Summary in English.)

11 Rantavaara A, Haukka S. Radioactivity of milk, meat, cereals and other agricultural products in Finland after the Chernobyl accident in 1986. Report STUK-A58. Supplement 3 to Annual Report STUK-A55. Helsinki: Finnish Centre for Radiation and Nuclear Safety, 1987.

12 Riihimäki V. Hunters' Central Organization. Personal communication.

13 Rissanen K, Rahola T, Hiukka E, Alftan A. Radioactivity of reindeer, game and fish in Finnish Lapland after the Chernobyl accident in 1986. Report STUK-A63. Supplement 8 to the Annual Report STUK-A55. Helsinki: Finnish Centre for Radiation and Nuclear Safety, 1987.

14 Salo A, Saxen R, Puhakainen M. Transport of airborne 90Sr and 137Cs deposited in the basins of the five largest rivers in Finland. Aqua Fennica 1984; 14,1: 21-31.

15 Saxen R, Rantavaara A. Radioactivity of fresh water fish in Finland after the Chernobyl accident in 1986. Report STUK-A61. Supplement 6 to Annual Report STUK- A55. Helsinki: Finnish Centre for Radiation and Nuclear Safety, 1987.

16 Sinkko K. Computer analysis of gamma spectra in sample measurements. Licentiate's dissertation. Helsinki: Helsinki University Department of Physics, 1981. (In Finnish. ) 28

17 Sinkko K, Aaltonen H. Calculation of the true coincidence summing correction for different sample geometries in gamma-ray spectroscopy. Report STUK-B- VALO 40. Helsinki: Finnish Centre for Radiation and Nuclear Safety, Surveillance Department, 1985.

18 Törmä O. Helsinki University Institute of Meat Technology. Personal communication.

19 Valkohäntäpeuran metsästyksen tulos 1986. Metsästäjä 1987; 1:5. (In Finnish.) 29

Fig. ] Division of the Finnish municipalities into five "p*oc;ories according to the estimate of the average 137 Cs deposition caused by the Chernobyl fallout.1 Fallout category Deposited 137 Cs (kBq nr2 on October 1, 1986) 1 0 4.3 2 4.4 - 10.1 3 10.2 - 21.7 4 21.8 - 45.0 5 45.1 - 67 i

30

Fig. 2 Game management districts and the province of Aland.

Oulu / ^S Kainuu r\ Ruotsalainen ( Pohianmaa^ y^-v/ "Jr^ r ^Northern f/ohjaiWa ^aVO >°rthern \( ^v-CentralL-v A^arelia inland* ^ A ^ ^ , . , X \ Southern Jv $ ^Norf^iern/ ^-\-^\ 0\ ,,Sav„ o _/Jy/

( ? HämejH. Kvnu/ VUJLOJL UusimaaV^V

Fig. 3 Sampling locations of moose. 31

Sampling locations of cervids other than moose. • White-tailed deer * Roe deer ,Jil3 reindeer • Fallow deer

Fig. 5 Sampling locations of hare. • Arctic hare * Brown hare v Species unknown 32

Sampling locations of waterfowl. • Mallard • Teal o Goldeneye • Wigoon • Goosander - Coot

Fig. 7 Sampling locations of terrestrial game birds • Wood pigeon • Capercaillie • Black grouse « Willow grouse • Hazel hen 33

CS-134

CS-131

Fig. 8 Arithmetic means for radloceslum contents' In moose meat samples from locations belonging to five different fallout categories (cf. Fig. 1). 34

12 3 4 ALAND NORTHERN KARELIA

OULU

D CS-134 0 CS-131 1. H008S 2. Cervlds other than moose 3. Hares 4. Waterfowl 5. Terrestrial game birds

Pig. 9 Estimates for areal and nationwide mean contents of radlocesium In different types of game meat. 134Cs has been given corrected to the date 1 October 1986. 35

12 3 4 12 3 4

VARSINAIS-SUOMI SATAKUNTA

1 2 3

SOUTHERN HÄME

Bq kg 1500_

1250 _

1000 _

150 _

500 _

250 _ oL_ 1 2 3 NORTHERN HÄME KYMI

Fig. 9 Estimates for areal and nationwide mean contents of radiocesium in different types of game meat. 134Cs has been given corrected to the date 1 October 1986. Continued. 36

1 2 3 * 12 3 4 SOUTHERN SAVO NORTHERN SAVO

12 3 4 1 2 3 CENTRAL FINLAND POHJANMAA

12 3 4 5 12 3 4 RUOTSALAINEN POHJANMAA NATIONWIDE MEAN

Fig. 9 Estimates for areal and nationwide mean contents of radiocesium in different types of game meat. 134Cs has been given corrected to the date 1 October 1986. Continued. 37

TF ,,a/ltg o.:«-

0.13- X K X X Adult e e e c*ir 0.12-

0.11- X 0.10- X 0.09' X 0.08- X 0.07- X 0.06- X e 0.05- X X e 0.04- X X a.03- 8 X X x 0.02- ox e x

0.01-

0.00" 1 1 i i i i 1MAY 1JUN 1JW. 1AUG 1SEP

Sampling date in 1986

Fig. 10 Transfer of fallout radiocesium to moose meat (values of TF from equation 1) at different sampling times.

jp m /kg N 0.07 60 ' XXX Adult X e e a c»if m C) 50 0

- 40-

30

X (l«) 20-

(13) Ctlf (17) I") < 6 © Adult 10: 0.01 <- ('<) x x P°> (53)

OH, xx xxx xxx 1— ., ...„,j I I T —r* ~i ' r •>—i—•—i—<—i—'—r1 0.00 0.01 0.02 0.03 0.04 0.03 0.06

TF m /kg

Fig. 11 Fig. 12 Monthly means of radiocesium Frequency distribution of transfer factors for moose. TF for transfer of radio­ The number of measurements cesium from fallout to included in each mean is given moose meat sampled after 20 in parentheses. The values June 1986. chosen for estimating areal con­ tents are shown by arrows. 3fl

3.0 % (13.8 %)

4.3 % 1.3 % (17.0 %) / (4.6 %)

6.1 (4.6 6.1 % 11.4 % (5.9 %) 2.2 % (8.0 %) (4.8 %) /12.0 % (5.9 %) 6.6 % (5.6 %)

9.4 % 5.8 % 0.4 % .(4.5 %)/ (1 JU? *)<&!f(4.9 %)' 3.7 % (3.9 %!

Fig. 13 Contributions of different game districts to the dietary radiocesium received via game meat of the hunting year 1986-1987. Contributions to the annual game bag are given in parentheses. 39

Type of game meat Fallout areas

137Cs: 1400 MBq

134Cs: 570 MBq

2 3

Annual game bag (edible meat): 6900 tons

1: Moose A: Main fallout 2: Cervids other rroa than moose 3: Hares B: Area of 4: Waterfowl minor 5: Terrestrial deposition game birds

Contributions of different types of game meat and different fallout areas to the dietary radiocesium received via game, and to the annual game bag in 1986- 1987. 40

Table I. Names of game animal species and groups included in sampling.

English Latin Finnish

Cervids Cervidae Hirvieläimen Moose Rices alces Hirvi White-tailed deer Odocoileus vlrginianus Valkohäntäpeura

Roe deer Capreolus capreolus Metsäkauris Fallow deer Dama dama Kuusipeura

Wild reindeer" Rangifer tarandus fennlcus Metsäpeura

Hares Leporldae Jäniseläimet Arctic hare Lepus timldus Metsäjänis Brown hare Lepus europaeus Rusakko

Waterfowl - Vesilinnut

Mallard Anas platurhynchos Heinä- eli sini sorsa Teal Anas crecca Tavi

Goldeneye Bucephala clangula Telkkä Wigeon Anas penelope Haapana Goosander Hergus merganser Isokoskelo Coot Fullca atra Nokikana

Terrestrial game birds - Metsä- ja pelto linnut

Black grouse Tetrao tetrlx Teeri Hazel hen Bonasla bonasla Pyy Willow grouse Lagopus lagopus Riekko Wood pigeon Columba palumbus Sepelkyyhky

• Not hunted in Finland. 41

Table II. Radlocesium contents in moose samples.

Cane Municipality Date of Cesium-134 Ceeium-137 Sex Age district •sapling Bq/kg Bq/kg in 1986

ALAND

Brando 28/10 31 85 Cow Adult Lemland 02/11 0 21 Bull Calf Lemland 02/11 15 58 Bull Adult Aland (14) " 02/11 30 79 - -

VARSINAIS-SUOMI

Halikko 27/07 50 101 - - 17/08 113 240 Cow Adult Kemiö 20/08 12 33 Cow Adult 11/07 23 53 Bull Adult Kuatavi 31/08 207 420 Cow Calf 02/09 140 292 Bull Calf 09/07 80 163 Bull Adult 27/08 62 121 - Calf Mynämäki 26/06 174 348 Cow Adult Mynämäki 27/07 612 1220 Cow Adult 10/07 86 168 Cow Adult Pöytya 17/07 59 122 Cow Adult 18/06 320 587 - Adult Tarvasjoki 01/09 31 74 Cow Adult 05/09 34 72 Bull Adult Uusiksupunki 02/08 233 453 Cow Calf b 02/08 147 281 Cow Adult Uusikaupunki 04/08 410 815 Cow Calf Uusikaupunki 18/10 510 1090 - Calf Uusikaupunki 18/10 394 843 Bull - Uusikaupunki 19/10 226 472 Cow - Uuaikaupunki 01/11 465 988 Bull Calf

SATAKUNTA

Eura 11/08 77 151 Bull Adult 31/08 56 122 Cow Adult 08/09 119 239 Cow Calf HJtoeankyro 17/07 157 297 Bull Adult Hämeenkyrö 21/07 166 305 Bull Calf 21/07 146 279 Cow Adult Parkano 14/07 294 578 Cow Adult Parkano 21/07 398 744 - Calf Parkano 09/09 248 519 Bull Adult Sakyla 28/06 111 209 Bull Adult Sakyii 10/08 58 122 Bull Adult

Number of individuals in combined samplaa ia glvan in paranthaaaa. The milk of thla cow contained 79 Bq cesium-134 and 146 Bq ceaium-137. 42

Table II. Radiocesium contents in moose samples. Continued.

Gam Municipality Date of Cesiua-134 Cesium-137 Sex Age district •aapling Bq/kB Bq/kfl in 1986

UUSIMAA

Espoo 13/08 22 50 Cow Adult 04/09 16 43 Cow Adult Karjaa 12/09 8 25 Bull Calf Kirkkonuaaii -6/05 177 324 - - Kirkkonummi 10/05 126 231 - - Lohja 31/05 142 278 - - Loviisa 16/07 104 198 Cow Adult Nummi -Pusula 31/08 31 71 Bull Adult Nurmijärvi 24/05 155 306 - - NurmiJirvi 23/07 77 154 Cow Adult Pernaja 16/07 187 363 Cow Calf Pernaja 16/07 64 128 Bull Adult Porvoo 11/08 28 68 Bull Adult Porvoo mlk 27/05 342 616 - - Porvoo alk 12/07 42 84 - - Ruotsinpyhtää 20/07 212 415 Cow Adult Sipoo 02/09 54 114 Bull Adult T sinisaari 24/07 16 46 Bull - Taamisasri 06/09 6 16 - Adult Tuusula 15/09 15 31 Bull Adult 02/09 15 37 Cow Adult Vihti 06/09 21 45 Bull Adult

SOUTHERN HAKE

Asikkala 23/07 299 560 Cow Adult Porssa (2) 28/07 170 350 Cow - Forssa 12/09 129 260 Bull Adult 09/07 269 498 Bull Calf Hattula 02/08 191 361 Bull Calf 03/08 130 235 Cow Adult Hauho 17/08 97 180 Cow Adult Hausjärvi 20/08 57 113 Bull Adult 28/08 23 54 Cow Adult Hollola 11/09 27 55 Cow - 01/08 90 173 Bull Adult Laimi 24/05 496 899 - - Laimi 20/07 218 413 Cow Adult Laimi 10/08 465 887 Cow Adult Lammi 26/08 309 603 Bull Calf 31/07 64 133 Bull Adult Nastola 03/09 221 429 . _ 43

Table II, Radiocesium contents in moose samples. Continued.

Came Municipality Date of Ceaium-134 Ceaium-13? Sex Age district sampling Bq/kg Bq/kg in 1986

SOUTHERN HAMS

Padasjoki 25/06 453 812 Bull - 14/08 204 410 Bull Calf 05/09 28 73 Bull Adult Tammela 05/07 161 329 Cow Adult Tammela 28/07 191 404 Cow Calf Tammela 29/07 149 296 Cow Adult Tammela 22/08 217 429 - - Tammela 02/09 51 108 Cow Adult 15/07 196 380 Bull Calf

NORTHERN HAME

Juupajoki 12/09 210 420 Bull . Kangasala 23/08 489 960 Cow Cair Kangasala 06/09 330 640 Bull Adult Kangasala 07/09 72 143 Bull Adult 29/08 587 1120 Cow Adult Kuru 29/07 137 256 Bull Adult LempMla 05/07 204 382 - - Längelmäki 25/07 305 553 Cow Adult Mäntti 21/07 275 497 Cow Adult 19/07 267 483 Cow Adult Orivesi 23/08 216 427 Cow Adult 28/08 165 323 Cow Adult Pilkan* 11/07 156 290 Bull Adult 18/07 252 463 Cow Adult Taapare 16/06 421 761 - - 08/07 305 578 - - Tampere 04/08 361 697 Cow Adult Tampere (2) 17/08 142 260 Cow Adult Tampere 24/08 282 545 - - Tampere 24/08 281 550 Cow Adult 13/08 355 675 Bull Calf Vilppula 20/08 95 176 Cow - Virrat 10/07 184 363 Bull Adult Ylöjärvi 08/09 390 790 Bull Adult yifijlrvi 09/09 179 359 Bull Adult 44

Table II. Radiocesium contents in moose samples. Continued.

Municipality Date of Cesium-134 Cesium-137 S«x Age district sampling Bq/kg Bq/kg in 1986

KYMI

Anjalankoaki (2) 21/06 114 215 Anjalankoaki 28/08 116 214 Cow Adult Elialki 28/06 174 326 14/07 20e 388 Bull Calf Iitti 10/10 93 194 Bull Adult 10/07 56 114 Bull Calf 06/08 382 724 Cow Adult Kotka 07/08 295 567 Cow Adult Kotka 07/08 378 713 Bull Adult Kotka 09/08 394 743 Bull Calf Kotka 25/08 212 415 Cow Calf 12/08 114 240 Cow Calf Lappeenranta (4) 22/07 20 47 Bull - Ruokolahti 10/08 9 34 Cow Adult Ruokolahti 13/08 6 23 Bull Adult 23/07 65 120 Cow Adult Valkeala 25/07 83 164 Bull - Valkeala 06/08 129 245 Cow Adult Vehkalahti 12/07 103 201 Cow Adult Vehkalahti 07/08 127 238 Cow Adult Vehkalahti (2) 17/08 70 141 Cow Adult Vehkalahti 29/08 139 274 Cow Adult 171 Vehkalahti 06/09 61 Bull Calf

SOUTHERN SAVO

Hartola 06/09 ies 360 Bull Adult mlk 28/07 271 514 Cow Adult 24/07 33 74 Cow Calf 01/09 Juva 13 33 Bull Adult Kangasniemi 27/07 56 120 Bull Adult Kangasniemi 14/08 96 193 Cow Adult Kangasniemi 19/08 38 91 Cow Adult Kerimäki 06/07 63 136 Bull Adult 22/08 14 45 Mäntyharju 02/09 48 98 Cow Adult Mäntyharju 05/09 14 38 Bull Adult 09/07 99 195 Bull Calf Savonlinna 02/08 16 41 Cow Adult 45

Table II. Radiocesium contents in moose samples. Continued.

Gan* Hunieipality Data ot Cesiim-134 Cesiuai-137 Sex Age district aaspling Bq/kg Bq/kg in 1986

NORTHERN SAVO

lisalai 10/07 22 49 Cow Adult 17/07 24 67 Bull Calf Lapinlahti 30/06 38 92 Cow Adult Lapinlahti 28/07 21 54 Cow Adult Leppävirta 22/08 55 105 Bull Adult Leppävirta 02/09 78 158 Bull Adult Rautalaani 12/09 93 170 Cow Adult Siilinjärvi 25/07 22 45 Cow Adult Sonkajärvi 04/08 21 56 Cow Adult Suonenjoki 03/07 125 243 - Adult Suonenjoki 05/07 125 252 - - Vieresi 27/07 17 4t Cow Adult

CENTRAL FINLAND

.'yvaskyla 04/06 220 402 - - Jyväskylä 05/09 49 106 - - Jassa 07/07 250 452 Cow Adult Jiwsl 28/07 176 330 Bull Adult Jaaal 13/09 85 175 Cow Adult 03/07 122 225 - - Keuruu 05/09 77 160 Cow Adult Konginkangas 21/07 114 228 - Calf Konginkangas (3) 01/08 164 315 - - Konginkangas 10/08 146 286 Cow Adult Korpilahti 28/08 40 83 - - Leivouaaki 21/07 31 78 Cow Adult Pylkonnaki 18/07 328 633 Cow Adult Pylkonnaki 27/08 116 230 Bull Adult Saarijärvi 29/08 116 227 Bull Adult 19/07 299 645 Bull Adult Uurainen 96/09 203 409 Cow Adult Viitasaari 09/07 118 235 Cow Adult Viitasaari 24/08 64 135 Cow Adult Äänekoski 19/07 113 214 Cow Adult 46

Tabic II. Radiocesium contents in moose pamni.es. rv--•»--• -•

Game Municipality Date of Cesium-134 Cenium-137 Sex Age district sampling Bq/kg Bq/kg in 1986

POHJANMAA

Ilmajoki 26/07 72 148 Bull Adult 06/08 70 136 Cow Calf 29/10 220 460 Cow Adult Jalasjärvi 05/09 95 223 Cow Calf 30/06 187 345 - Adult Kauhajoki 18/08 107 227 - - Kälviä 06/09 37 82 Cow Adult 17/08 71 147 Cow Adult Nurmo 06/09 133 280 Bull Adult Seinäjoki 03/06 882 1610 - - Seinäjoki 08/08 79 170 Cow Adult Seinäjoki 13/08 105 222 Cow Adult Töysä 30/08 79 179 Bull Calf Ähtäri 29/07 92 178 Cow Adult

RUOTSALAINEN POHJANMAA

Kruunupyy 02/06 584 1030 - calf Maalahti 09/07 91 187 Cow Adult Mustasaari 21/09 490 970 Bull Calf Närpiö 18/07 101 189 Bull Adult Pietarsaari mlk 27/05 795 1390 01/09 62 135 Uusikaarlepyy 02/08 329 610 Bull Adult Uusikaarlepyy 11/0* 141 286 - Adult Uusikaarlepyy 13/09 141 290 - Calf Uusikaarlepyy 22/09 164 340 Cow Adult Uusikaarlepyy 22/09 260 570 Bull Calf Uusikaarlepyy 23/09 190 380 Bull Adult Vöyri 09/07 483 889 Cow Calf

NORTHERN KARELIA

Ilomantsi 21/08 21 Cow Adult 05/08 14 44 Cow Calf 12/07 24 Bull Adult 08/09 21 Bull Adult . Värtsilä (2) 17/08 20 - - Tohmajärvi 29/06 16 35 - - 47

Table II. Radiocesium contents in moose samples. Continued.

Game Municipality Date of Cesium-134 Cesium-137 Sex Age district sampling Bq/kg Bq/kg in 1986

OULU

07/09 4 14 Cow Adult 01/08 3 28 Bull Adult Ii 08/09 2 13 Bull Adult 02/09 12 31 - - Kalajoki 05/09 8 22 Cow - Kalajoki 05/09 17 51 Bull - 25/07 5 30 Bull Adult Kiiminki 13/09 4 18 Cow Adult 02/08 4 45 Bull Adult KSrsamMci 03/09 4 16 - - Merijärvi 15/09 5 19 - - Oulu 09/07 6 59 Bull Adult Oulu 24/07 5 44 Co» Adult Oulu 26/07 5 31 Bull Adult Pudasjärvi 15/07 3 65 Bull Adult Pudasjärvi 23/08 8 57 Cow Adult Pudasjärvi 06/09 2 24 Cow Adult Pyhäjoki 15/07 4 18 Cow Adult Pyhäjoki 28/07 8 29 Cow Adult Pyhäjärvi. (2) 21/07 16 44 - - 08/09 4 24 Cow Adult 22/07 8 33 Bull Adult 20/07 1 14 Bull - Utajärvi 03/09 3 25 Bull Adult 08/07 3 29 Cow Adult Vaala 02/08 2 21 Cow Adult Vaala 05/08 3 24 Bull Adult Ylikiiminki 16/08 5 57 Cow Calf Ylivieska 23/06 22 53 - - Ylivieska 04/09 13 41 - Calf Ylivieska 04/09 15 35 Cow Adult Ylivieska 09/09 10 28 Bull Calf 48

Table II. Radiocesium contents in moose samples. Continued.

Cane Municipality Date of Cesium-134 Cesium-137 Sex Age district stapling Bq/kg Bq/kg in 1986

KAINUU

Kajaani 17/07 14 45 Bull Adult 22/08 5 18 Bull Adult Kajaani 26/08 11 36 Cow Adult Kuha» 23/08 15 41 Bull Adult Paltamo 04/08 2 21 Cow Adult Puolanka 13/07 4 23 Bull - 27/08 27 66 Cow Adult Sotkamo 28/08 43 105 - Calf Sotkamo 07/09 44 113 Cow Adult Sotkamo 12/09 28 72 Bull Adult 02/08 2 16 Bull Adult Suomussalmi 10/08 2 14 Bull Adult Suomussalmi 25/10 32 87 Suomussalmi 12/11 40 100

LAPLAND

Kemi 11/07 4 21 Bull Adult Kemi 11/07 4 31 Bull Adult Kemi 20/08 3 21 Cow Adult Kemi 21/08 4 10 Kemi 10/09 0 23 Keminmaa 01/07 10 82 Cow Aduit Keminmaa 21/07 8 73 Cow Adult 07/03 7 16 Bull Adult Rovaniemi mlk 30/07 4 25 Bull Adult Rovaniemi mlk 10/08 6 26 Cow - Rovaniemi mlk 11/08 6 58 Rovaniemi mlk 10/09 4 18 Bull Adult Rovaniemi mlk 11/09 2 13 - Calf 07/08 4 18 Bull Adult Sodankylä 28/06 9 18 - - Tornio 09/08 0 10 Cow Adult Tornio 06/09 6 60 Cow Adult

<•- Means and ranges for samples from Lapland have been given in the report STUK A63. 49

Table III. Radiocesium contents in samples of cervids other than moose.

Species district, Date of Cesium-134 Ceaium-137 municipality sampling Bq/kg Bq/kg in 1986

White-tailed deer

SOUTHERN HAME

Forssa 16/08 77 176 Hollola 03/09 171 324 H «seiniinne 20/07 229 478 02/08 46 95 Janakkala, le •la (2) 11/08 114 250 14/09 169 420 Urjala 17/08 177 354

NORTHERN HÄME

Nokia 29/07 223 434

SATAKUNTA

Huittinen 27/08 73 158 Huittinen 09/09 361 760 Kokemäki 24/07 76 154 Kokemäki 03/09 188 406 09/08 150 305 16/08 138 267 Vammala 14/09 979 1954 Vammala 14/09 500 1025 Aetaa 14/07 85 153

UUSIKAA

Vihti 09/07 72 152

VARSIHAIS-SUOMI

Halikko 14/08 23 52 Halikko 14/08 28 60 Halikko 25/08 27 62 Halikko 13/09 161 431 Loimaa 05/09 377 775 11/07 104 216 Oripli 01/09 329 679 Pyhäranta 29/06 223 457 POytyl 10/07 99 197

a Number of individuals in combined samples is given in parentheaes. 50

Table III. Radiocesium contents in samples of cervids other than moose. Continued.

Species Gaae district. Date of Ceaiua-134 Cesiun-137 Municipality •aaipline Bq/kg Bq/kg in 1986

Fallow deer

UUSIMAA

Inkoo 21/08 41 125

Roe deer

ALAND

H til—ar land 25/08 59 159 Jomala 15/07 11 24 Lemland 26/08 29 66

SOUTHERN HAME

Hollola 18/08 33 79

Wild reindeer

POHJANMAA

Ahtlri 05/09 281 529 51

Table IV. Radiocesium contents in samples of hare.

Species Game district Municipality Date o? Cesium-134 Cesium-137 sampling Bq/kg Bq/kg

Brown hare

Southern Hame Hollola 20/08 17 32 Southern Hame Hollola 20/08 15 28 Southern Hame Hollola 26/08 27 47 Southern Häme Lammi 23/08 26» 474 Kymi Valkeala 25/07 31 53 Satakunta Kankaanpää 03/09 671 1408 Uusimaa Helsinki 11/09 0 3

Arctic haro

Northern Häme Kuru 29/07 679 1252 nuuiaominen .or janmaa Mustasaari 07/09 605 1164 riubOKUIIK Harjavalta 01/09 443 908 Satakunta Ikaalinen 07/09 313 608 Satakunta Vammala 06/09 438 902 Varsinais-Suomi Uusikaupunki 13/09 926 1888

Hare

Southern Hame 22/08 873 1593 Northern Hame Kuru 16/08 84 156 Southern Savo Nikkelin mlk 05/09 12 49 Northern Karelia 31/07 5 21 Oulu 11/09 7 42 Oulu Kuusamo 14/09 7 59 Pohjanmaa Lohtaja 20/09 85 210 Pohj anmaa Soini 01/09 142 272 Ruotsalainen Pohjanmaa 25/08 51 97 Uusimaa Porvoo 14/08 6 11

a Species unknown. 52

Table V. Radiocesium and 110»Ag contents in samples of water- fowl.

Species Caste district nunicipality Number of Date of Cesium-134 Cesium-137 Silver-110m individuals sampling Bq/kg Bq/kg Bq/kg

Coot Southern Häme Hollola 1 29/07 87 178 86 Southern Kane Hollola • H 29/07 70 132 71 Southern Häme Hollcla 1 20/08 13 43 30

Goldeneye Southern Hame Tammela 1 20/08 87 193 0 Southern Hame Lammi 1 11/08 1144 2136 107 Southern Hame Lammi 1 23/08 3608 6861 0 Central Finland Keuruu 1 22/08 110 260 0 Central Finland Kivijärvi 2 20/08 314 586 6 Northern Hame Kangasala 1 26/08 64 153 0 Northern Häme Kuru 2 16/08 797 1514 24 Northern Hame Virrat 1 20/08 63 151 31 Pohjanmaa 1 20/08 42 83 0 Pohjanmaa Kuortane 1 21/08 45 81 0 Pohjanmaa Laihia 1 20/08 0 0 0 Pohjanmaa Lehtimäki. Soini 3 20/08 311 599 17 Satakunta Karvia. Parkano 6 15/08 900 1734 175

Goosander Ruotsalainen Pohjanmaa Vaasa 23/09 30 77

Mallard Southern Kame Hollola 41 20/08 43 87 7 Southern Hlme Hollola 1 24/08 329 624 0 Southern Hame Tammela ;! 20/08 185 386 0 Southern Hame Lammi 1L 06/08 1448 2679 0 Southern Hame Lammi ]L 06/08 2529 4673 79 Southern Hame Lammi 1L 08/08 1765 3208 41 Southern Hame Lammi 1L 08/08 1973 3674 24 Southern Hame Lammi ]L 08/08 1246 2349 16 Southern Häme Lammi 1L 24/08 1616 3178 28 Kymi Valkeala L 25/07 26 64 0 Kymi Valkeala L 25/07 28 56 0 Northern Häme Kangasala L 06/09 306 569 0 Northern Häme Kangasala L 07/09 441 860 0 Pohjanmaa Isokyrö L 22/08 17 32 0 Pohjanmaa Kuortane l 21/08 70 138 0 Pohjanmaa Laihia 3 20/08 10 16 0 Pohjanmaa L 20/08 831 1648 0 Pohjanmaa Lohtaja L 23/08 14 25 0 Satakunta Karvia, Parkano l 15/08 423 802 7 Uusimaa Siuntio L 20/08 0 0 0 53

Table V. Radiocesium and 110,»Ag contents in samples of water­ fowl. Continued.

Species Game district Hunicipality Number of Date of Cesium-134 Cesium-137 Silver-llOm individuals 3ampling Bq/kg Bq/kg Bq/kg

Teal Southern Hame Tammela 1 21/03 313 593 0 Southern Hame Hollola 1 23/08 29 90 0 Southern Hame Lammi 1 05/08 1272 2334 0 Southern Hame Lammi 1 05/08 2209 4165 28 Southern Hame Lammi 1 08/08 525 1005 C Southern Hame Lammi 1 08/08 2317 4349 30 Southern Hame Lammi 1 08/08 222 432 0 Central Finland Kivijärvi 1 20/08 393 847 0 Northern Häme Kangasala 1 24/08 163 324 0 Northern Hame Virrat 3 20/08 187 357 6 Northern Häme Virrat 1 24/08 1260 2522 0 Pohjanmaa Lehtimäki. Soini 3 20/08 334 620 15 Pohjanmaa Peräseinäjoki 1 20/08 84 148 28 Pohjanmaa Ähtäri 1 21/08 81 193 0 Satakunta Karvia 1 18/08 809 1664 0 Uusimaa Hyvinkää 5 10/08 19 39 0 Uusimaa Hyvinkää 1 23/08 48 87 0

Wigeon Central Finland Kivijärvi 1 20/08 2520 4861 0 Pohjanmaa Ähtäri 1 21/08 210 373 0 54

Table VI. Radiocesium contents in samples of terrestrial game birds.

Species Game diatrict Municipality Number of Date of Cesium-134 Cesium-137 individuala sampling Bq/kg Bq/kg

Black grouae

Southern Häme Hollola 2 23/08 115 218 Northern Häme Kuru 1 16/08 330 662

Hazel hen

Southern Häme Lammi 1 25/08 390 764

Hazel hen and capercaillie

Pohjanmaa Soini 3 25/08 255 548

Capurr s.. Lie

Lapland Rovaniemi 1 03/08 15 94

Willow grouse

Oulu Kuusamo 1 20/09 3 12

Wood pigeon

Southern Häme Hollola 1 29/07 163 345 Northern Häme Kuru 1 30/07 194 353 Pohjanmaa Laihia 1 20/08 24 42 Uusimaa Hyvinkää 1 10/08 50 120 Varsinaia-Suomi 2 15/08 9 19 55

Table VII. Short-lived, occasionally detected radionuclides in moose meat samples in Bq kg"1 . The error of determination is one standard deviation.

l31 Game district, Date of 12 9m «po I 132Te 136 es municipality sampling 34 d 8 d 76 h 13 d

Varsi nai s-Suoari.

Kalanti 17.8. 87 + 22 % 0s 0 0

Ikjsimaa

Kirkkonummi 10.5. 84 + 19 % 231 + 5 % 67 + 7 % 32 + 9 % _«_ 10.5. 70 • 25 % 137 + 4 % 31 + 8 % 26 + 9 % Nurmijärvi 24.5. 0 46 + 16 % 0 0 Nurmijärvi 23.7. 23 + 36 % 0 0 0 Porvoon mlk 27.5." 0 42 + 28 % 0 23 + 48 % Lohja 31.5. 0 12 + 14 % 0 9 1 23 %

Southern Hame

Lammi 24.5. 0 50 + 15 % 0 44 + 16 % Hauho 3.8. 45 + 28 % 0 0 0 Tanmela 5.7. 74 + 25 % 4 + 33 % 0 0

Kymi

Kotka 6.8. 118 + 16 % 0 Kotka 7.8. 64 + 23 % 0

Central Finland

Jyväskylä 4.6. 8 + 21 % 13 + 19 %

Southern Savo

Kangasniemi 19.8. 36 + 29 % 0

Ponj annaa

Seinäjoki 3.6. 28 + 10 % 0 56 + 7 % Töysä 30.8.c 0 0 0

Ruotsalainen Pohjanmaa

Pietarsaari mlk 27.5. 0 78 +20 % 0 66 + 18 % Kruunupyy 2.6. 0 26 + 15 % 0 33 + 18 %

8 Below the detection limit, which varied. b 1 103 The sample oontalned 13 Bq kg" (+29 %) Ru (T1/2 = 39 d). c 1 ,5 The sample contained 6 Bq kg- (+ 18 %) Nb (T1/2 = 35 d). 56

Table VIII. TF values for transfer of radiocesium from fallout to different types of game meat. Arithmetic means, medians and ranges of sample-specific transfar factors from equation 1, in m2 kg-1 .

Period I: spring before 20 June Period II: summer and autumn after 20 June

Species or group Arithmetic Min - max of game animals, mean; median sampling period, (number of locations or samples)

Moose, adults

I (11) 0.07; 0.07 0.015 - 0.13 II (216) 0.0097; 0.0074 0.001 - 0.06

Moose, calves I (1) 0.06; - II (43) 0.015; 0.010 0.002 - 0.080

White-tailed deer II (27) 0.017; 0.013 0.0G5 - 0.031

Hares II Arctic hare (6) 0.04; 0.04 0.01 - 0.09 Brown hare (6) 0.01; 0.002 0.001 - 0.05

Terrestrial birds

II (9) 0.01; 0.01 0.003 - 0.02

Waterfowl II (43)a 0.03; 0.01 0.001 - 0.13

a A rough estimate, 0.003, was used for coastal waterfowl. Table IX. Arithmetic means and calculated areal means (cf. equation 2) for 13 7 Cs contents in moose meat from different game districts before the hunting season of 1986, in Bq kg*1 .

Game district Number of Arithmetic Calculated measurements mean areal mean

Aland 4 60 40 Varsinais-Suomi 22 410 170 Satakunta 11 320 310 Uusimaa 22 170 160 Southern Häme 26 360 340 Northern Häme 25 510 530 Kymi 23 280 230 Southern Savo 13 150 200 Northern Savo 12 110 150 Central Finland 20 280 350 Pohjanmaa 14 310 260 Ruotsalainen Pohjanmaa 13 560 260 Northern Karelia 6 30 40 Oulu 32 30 50 Kainuu 14 50 70 Lapland 17 30 40 FINNISH CENTRE FOR RADIATION AND NUCLEAR SAFETY P.O.Box 268, SF-00101 HELSINKI, FINLAND Institute of Radiation Physics (SFL) 1958 - 1975 Institute of Radiation Protection (STL) 1975 - 1984 Finnish Centre for Radiation and Nuclear Safety (STUK) since 1st March 1984 Report code prefix letters (representing the acronym of the Finnish name of the institution) have been changed with the names of the institution. Report numbers continue in the original progressive series.

SFL-A reports: SFL-A2 Castren, 0. Gammaspectrometric determinations of caesium-137 and potassium in Finnish milk. Helsinki, 1966. SFL-A3 Paakkola, O. Radiostrontium in milk, grass and some other biological samples in Finland. Helsinki, 1966. SFL-A4 Salo, A. Strontium-90 and caesium-137 in water in Finland. Helsinki, 1966. SFL-A5 Castren, O. An Algol programme for the detection efficiences around a cylindrical scintillation cristal. Helsinki, 1966. SFL-A6 Suomela, M. The construction and calibration of the whole- body counter in the Institute of Radiation Physics. Helsinki, 1967. SFL-A7 Toivonen, M. On routine personnel dosimetry with fluoroglasses. Helsinki, :1967. SFL-A8 Studies on environmental radioactivity in Finland. Annual report. Helsinki, 1967. SFL-A9 Bagge, P. and Salo, A. Biological detectors of ra­ dioactive contamination in the Baltic. Helsinki, 1967. SFL-A10 Isola, A. A portable survey meter for low-level radia­ tion measurements. Helsinki, 1967. SFL-A11 Toivonen, M. and Isola, A. On the exposure of radiolo­ gical employees in Finland during 1965-1967. Helsinki, 1968. SFL-A12 Studies on environmental radioactivity in Finland 1967. Annual report. Helsinki, 1968. SFL-A13 Toivonen, M. An arrangement for read-out of luminescent dosimeters. Helsinki, 1969. SFL-A14 Kahlos, H. Radon-222 concentration of some water samples determine with gammaspectronetric measurements. Helsinki, 1969. SFL-A15 Asikainen, M. and Blomqvist, L. Measurements of airborne radionuclide in Finland with a highvolume air sampler and Ge(Li)-spectroscopy. Helsinki, 1970. 2

SFL-A16 Kahlos, H. and Suomela, M. Studies on the elimination rate and the radiation exposure following ingestion of radon-222 rich water. Helsinki, 1970. SFL-A17 Studies on environmental radioactivity in Finland 1968- 1970. Annual report. Helsinki, 1971. SFL-A18 Rannikko, S., Uotila, I. and Kiviniitty, K. Measure­ ments of radiation output of telecobalt units in Finland. Helsinki, 1971. SFL-A19 Kahlos, H. and Asikainen, M. Natural radioactivity of ground water in the Helsinki area. Helsinki, 1973. SFL-A20 Salo, A. and Saxen, R. On the role of humic substan­ ces in the transport of radionuclides. Helsinki, 1974. STL-A reports: STL-A21 Studies on environmental radioactivity in Finland 1971- 1975. Annual report. Helsinki, 1977. STL-A22 Bjarland, B. The Hytype printer as versatile output device in small NOVA configurations. Helsinki, 1976. STL-A23 Uctila, I. CAMAC extension for BASIC on the NOVA 1200 minicomputer. Helsinki, 1976. STL-A24 Asikainen, M. and Kahlos, H. Natural radioactivity of ground and surface water in Finland = Pohja- ja pinta- vesien luonnollinen radioaktiivisuus Suomessa. Helsinki, 1977. STL-A25 Rannikko, S. J. and Sinitsin, R. V. (ed.). Clinical dosimetry: proceedings of the Soviet-Finnish Cooperati­ ve Meeting on Clinical Dosimetry, 6-10 December 1976, Leningrad USSR. Helsinki, 1979. STL-A26 Studies on environmental radioactivity in Finland 1976- 1977. Annual report. Helsinki, 1979. STL-A27 Toivonen, M. Individual TL detector characteristics in automated processing of personnel dosemeters: correction factors as extension to identify codes of dosemeter cards. Helsinki, 1979. STL-A28 Bjarland, B. Microcomputer control of automated TL reader. Helsinki, 1979. STL-A29 Stenstrand, K., Toivonen, H., Rytömaa, T. Radiation- induced chromosome aberrations in human lymphocytes: dose-response relationships after irradiation in vitro with 200 kV X-rays and 60-Co gamma rays. Helsinki, 1979. STL-A30 Toivonen, H. A flexible multipurpose model for normal and transient cell kinetics. Helsinki, 1980. 3

STL-A31 Toivonen, K. Transient cell kinetics. Applications of tracer techniques to cancer research and radiobiology. Helsinki, 1980. STL-A32 Studies on environmental radioactivity in Finland 1978. Helsinki, 1980. STL-A33 Rantanen, E. Calibration of neutron rem counters: discussion on different results obtained in two labora­ tories. Helsinki, 1980. STL-A34 Studies on environmental radioactivity in Finland 1979. Helsinki, 1981. STL-A35 Rannikko, S. Concept of the population mean malignancy dose. Helsinki, 1981. STL-A36 Rannikko, S., Heinämaa, R. Number of medical X-ray examinations, their distribution and doses to bone marrow in 1978. Helsinki, 1981. STL-A37 Rannikko, S. Problems concerning the assessment of the radiation dose to population as a result of X-ray examinations. Helsinki, 1981. STL-A38 Studies on environmental radioactivity in Finland 1980. Helsinki, 1981. STL-A39 Asikainen, M. Natural radioactivity of ground water and drinking water in Finland. Helsinki, 1982. STL-A40 Studies on environmental radioactivity in Finland 1981. Helsinki, 1983. STL-A41 Rajama, J., Rantavaara, A. Radioactivity in Finnish cereals from 1962 to 1980. Helsinki, 1982. STL-A42 Turai, I. and Toivonen, H. Radiohygiene of fission isotopes of iodine: experiments in rats and model studies in man. Helsinki, 1983. STL-A43 Servomaa, A., Toivonen, M. and Kiuru, A. Mailed TL dosimeters for monitoring the output from diagnostic x-ray equipment. Helsinki, 1983. STL-A44 Servomaa, A. Significance of x-ray diagnostic quality assurance in terms of radiation impact to patients. Helsinki, 1983. STL-A45 Suomela, M. Whole-body counter studies in radiation protection and clinical research. Helsinki, 1983. STL-A46 Arvela, H. A Nordic intercomparison and evaluation of the detector responses to natural environmental gamma radiation. Helsinki, 1983. STL-A47 Studies on environmental radioactivity in Finland 1982. Helsinki, 1984. 4

STL-A48 Studies on environmental radioactivity in Finland 1983. Helsinki, 1984. STUK-A reports: STUK-A49 Tarvainen, M. and Riihonen, M. Spent fuel measure­ ments at Loviisa nuclear power station. May, 1982. Helsinki, 1984. STUK-A50 Järvinen, H., Rannikko, S. and Servomaa, A. Report on the Nordic-Soviet meeting on standard and applied dosimetry. Helsinki 9-11 November 1983. Helsinki, 1984.

STUK-A51 Arvela, H. and Winqvist, K. Influence of source type and air exchange on variations of indoor radon concentration. Helsinki, 1986. STUK-A52 Ekenstam, G. af and Tarvainen, M. Independent burnup verification of BWR-type nuclear fuel by means of the x37Cs activity. Helsinki, 1987.

STUK-A53 Järvinen, H., Rantanen, E. and Jokela, K. Testing of radiotherapy dosimeters in accordance with IEC specification. Helsinki, 1986. STUK-A54 Studies on environmental radioactivity in Finland 1934-1985. Annual report. Helsinki, 1987.

STUK-A55 Studies on environmental radioactivity in Finland in 1986. Annual report. Helsinki, 1987.

STUK-A56 Sinkko, K., Aaltonen, H., Taipale, *. K. and Juuti­ lainen, J. Airborne radioactivity in Finland after the Chernobyl accident in 1986. Supplement 1 to annual report STUK-A55. Helsinki, 1987. STUK-A57 Saxen, R., Taipale, T. K. and Aaltonen, H. Radioactivi­ ty of wet and dry deposition and soil in Finland after the Chernobyl accident in 1986. Supplement 2 to annual report STUK-A55. Helsinki, 1987.

STUK-A58 Rantavaara, A. and Haukka, S. Radioactivity of milk, meat, cereals and other agricultural products in Finland after the Chernobyl accident in 1986. Supplement 3 to annual report STUK-A55. Helsinki, 1987.

STUK-A59 Rantavaara, A. Radioactivity of vegetables and mush­ rooms in Finland after the Chernobyl accident in 1986. Supplement 4 to annual report STUK-A55. Helsinki, 1987. STUK-A60 Saxen, R. and Aaltonen, H. Radioactivity of surface water in Finland after the Chernobyl accident in 1986. Supplement 5 to annual report STUK-A55. Helsinki, 1987. 5

STUK-A61 Saxen, R. and Rantavaara, A. Radioactivity of fresh water fish in Finland after the Chernobyl accident in 1986. Supplement 6 to annual report STUK-A55. Helsin­ ki, 1987.

STUK-A62 Rantavaara, A., Nygren, T., Nygren, K. and Hyvönen, T. Radioactivity of game meat in Finland after the Chernobyl accident in 1986. Supplement 7 to annual report STUK-A55. Helsinki, 1987. STUK-A63 Rissanen, K., Rahola, T., Hiukka, E. and Alfthan, A. Radioactivity of reindeer, game and fish in Finnish Lapland after the Chernobyl accident in 1986. Supple­ ment 8 to annual report STUK-A55. Helsinki, 1987. STUK-A64 Rahola, T., Suomela, M., Hiukka, E., Puhakainen, M. and Pusa, S. Radioactivity of people in Finland after the Chernobyl accident in 1986. Supplement 9 to annual report STUK-A55. Helsinki, 1987.

STUK-A65 Arvela, H., Blomqvist, L., Lemmelä, H., Savolainen, A-L. and Sarkkula, S. Environmental gamma radiation measurements in Finland and the influence of the meteo­ rological conditions after the Chernobyl accident in 1986. Supplement 10 to annual report STUK-A55. Helsin­ ki, 1987. STUK-A66 Hus, E., Sjöblom, K-L., Saxen, R., Aaltonen, H. and Taipale, T. K. Finnish studies on radioactivity in the Baltic sea after the Chernobyl accident in 1986. Supplement 11 to annual report STUK-A55. Helsinki, 1987. STUK-A67 Hus, E., Sjöblom, K-L., Aaltonen, H., Klemola, S. and Arvela, H. Monitoring of radioactivity in the environs of Finnish nuclear power stations in 1986. Supplement 12 to annual report STUK-A55. Helsinki, 1987.

STUK-A68 Puhakainen, M., Rahola, T. and Suomela, M. Radioacti­ vity of sludge after the Chernobyl accident in 1986. Supplement 13 to annual report STUK-A55. Helsinki, 1987. STUK-A69 Salmenhaara, S. and Tarvainen, M. Nondestructive measurements with a WWER-440 fuel assembly model using neutron and gamma sources. Helsinki, 1987. STUK-A70 Hellmuth, K-H. Rapid determination of strontium-89 and strontium-90 - experiences and results with various methods after the Chernobyl accident in 1986. Helsinki, 1987. ISBN 951-47-0493-2 ISSN 0781-1705