A review of the dietary intakes of chemical contaminants*

Bulletin ofthe WorldHealth Organization, 63 (5): 945- 962 (1985) © World HealthOrganization 1985 A review of the dietary intakes of chemical contaminants* H. GALAL GORCHEV' & CHARLES F. JELINEK2 Data on the dietary intakes of certain contaminants have been receivedfrom eleven collaborating centres participating in the Joint FAO/WHO Food Contamination Monitoring Programme. The data cover the period from 1971 to 1983 and include information on the intakes ofa series oforganochlorine and organophosphorus pesticides, polychlorinated biphenyls, cadmium, lead, and aflatoxins. When compared with the acceptable daily intake (ADI) or provisional tolerable weekly intake (PTWI) of the pesticides/contaminants in question, the data indicate that, in some countries, the exposure to certain organochlorine pesticides may constitute a significant portion ofthe ADI. Because of the concentration of these compounds in thefatty portions offood, a high animal fat intake will increase the dietary exposure to organochlorine compounds Dietary intakes ofcadmium and lead constitute an appreciable percentage oft he PTWI for these two contaminants. As the intakes of cadmium and lead per kilogram of body weight are highestfor infants and children, every effort should be made to reduce the levels of these two contaminants in thefood supply. INTRODUCTION Collection of data on contaminants in the diet is an activity of the Joint FAO/WHO Food Contamination Monitoring (FCM) Programme. This Programme forms part of the Global Environment This review article is based on data received from participants in the FAO/WHO Food Contamination Monitoring Programme, who are listed in Annex I on page 962. ' Scientist, Environmental Hazards and Food Protection, Division of Environmental Health, World Health Organization, 1211 Geneva 27, Switzerland. Requests for reprints should be sent to this author. 2 Deputy Director, Office of Physical Sciences, Center for Food Safety and Applied Nutrition, Food and Drug Administration, Washington, DC, USA. Monitoring System (GEMS) which was established by the United Nations Environment Programme. A request was made in 1979 to the FAO/WHO Collaborating Centres for Food Contamination Monitoring to submit all available data on the levels of certain chemical contaminants in the total diet and to provide details on how the total dietary intakes were determined. However, only since 1980 has this data collection been carried out in a systematic way. Information has been obtained on the estimated daily dietary intakes of contaminants selected for monitoring in the FCM Programme, such as aldrin and dieldrin, DDT complex, hexachlorobenzene (HCB), total hexachlorocyclohexane (HCH) isomers, lindane (gamma-HCH), heptachlor and heptachlor 4604 -945- H. G. GORCHEV & C. F. JELINEK C VO eggRC4 0 a, (V0Wa,'- '0 > o :3 a,.-va, LD 0) -. L. (A0MM, z z 02.0- u~ .0~~~~U)Lfl0 0 C' W 0 0 0 %.-~~ m 0 >. z 00 0 C~~~~~~~~~~~ > E 0 co a, Up". 0 -0- ~ aC') 0 E 0 a, &O > 0~~~~~~.C) 0 0 0 ;' ~ U )OLn 0 -)e a, .0&U) > Oa CV4 ( 0.~ ~ ~ ~~~~00 r- 0 U, 0 0 8 r-' C' 0 Q ._ 0.00 a,0 M . 0.0 + - 0. 0 .0 0 & 0 V0 0 .X Z Z 00 0 C V C V o~~~~~- C) 0C C V C V *-° _ Pc E^m @ n = ° .° E 0 > is 0° cQ O >> m C 1 Z- r < acU CC0)0 M > 0 > 0 ~~~0 -0 ~ ~E o0 'C) E 0) >V Z6 a, U) C a, 0 E)0 -a, CC a, 0.E a E -O C, @ .0D .C V V X E E -0 .- a0 a_CoV -C 0 a, C U._ a 946 -0) -L E m) CY) - m 0n CD O a) t- . M>S (1) 6 I- cn o V0E a,0 +, 'a 3 .E 0m C a, V a, C') Q N C a, m 0. I 'a CCD a) n- 3 0, C I E 0 0, . C a.,_Ca,Do- 0 & ._4-= V m C a)to > 4)0) <0 () -W C ._ C E C 0 C) 0 ax m -C C 0 ._ n a, V U) C . C 0 a, 0 C) C. 0 a, I- 0UW E E < .r <: m a, a, am ) cv U)c0 bt J 'E 4) N OU)0 > C1 2 m DIETARY INTAKES OF CHEMICAL CONTAMINANTS 947 epoxide, diazinon, malathion, parathion, parathion- methyl, polychlorinated biphenyls (PCBs), afla- toxins, cadmium, and lead. Data on these contami- nants in the diet were reported from collaborating centres in Australia, Austria, Canada, Guatemala, Hungary, Ireland, Japan, New Zealand, Sweden, the United Kingdom, and the United States of America. Austria, Ireland, and Sweden submitted dietary intake data on cadmium and/or lead only. The data received cover the period 1971-83. In order to identify potential health problems from the presence of toxic contaminants in the food supply, the extent to which the actual dietary intakes approach or exceed a toxicologically acceptable daily intake (ADI) or a provisional tolerable weekly intake (PTWI) has been made. The acceptable daily intake of a chemical is the daily intake which, even if consumed for an entire lifetime, appears to be without appreciable risk on the basis of all the known facts at the present time. It is expressed in this paper in micrograms of the chemical per kilogram of body weight (jsg/kg body weight). For this purpose, "without appreciable risk" is taken to mean the practical certainty that injury will not result even after a lifetime of exposure (1). The Joint FAO/WHO Meeting on Pesticide Residues has established ADIs for a number of pesticides used in food production. Similarly the Joint FAO/WHO Expert Committee on Food Additives has established ADIs for food additives. Since 1972, this Committee has also evaluated several food contaminants such as cadmium, lead, and mercury and allocated PTWIs rather than ADIs for these contaminants to emphasize among other things the permissible rather than the acceptable levels of intakes of these contaminants. For the protection of the health of an individual, the amount of a chemical residue consumed by that individual should not exceed the ADI or PTWI over a prolonged period of time. To ascertain whether a consumer is at risk or not, therefore, it is important to compare the estimated intake, as assessed by dietary intake studies, with the ADI or PTWI. The characteristics of the diet and the preparations for analysis varied widely from one country to another, and the approach employed in a given country depended on the resources available and on local food habits and consumption patterns. Table 1 summarizes the main characteristics of the dietary intake studies carried out by the different countries and is based on information provided by the Collaborating Centres for the FCM Programme and on other published and unpublished data (2-9),a as well as information contained in the Guidelines for a Japan. Summarized results of total diet study, 1979. Unpub- lished document. the study ofdietary intakes ofchemical contaminants (10). Some countries have submitted intake data for several population groups. For example, intake data from Australia were related to infants (9 months old, average weight, 9.5 kg), 2-year-old children (average weight, 12.25 kg), women (average weight, 58 kg), etc. Hungary submitted data for a variety of consumer groups of different ages and sex (e.g. boarding schoolchildren, inmates of old people's homes). From the values submitted in ,sg/person/day, the corresponding intakes per kilogram of body weight have been calculated in each case. It should be noted that no country has submitted dietary intake data on all the contaminants included in the Food Contamination Monitoring Programme. In the case of total diet programmes involving collection of "market baskets".,b the data are based on annual analysis of a number of market baskets ranging up to 24 per year. Some of the data go back to dietary intake studies carried out in 1971. The submission of data from the USA for the most recent period included the dietary intake data developed for all of 1981 and the first quarter of 1982. For purposes of simplification this will be referred to as 1982 data. Dietary intake data collected between 1971 and 1979 have been summarized and assessed. c The present document reports on these as well as on the recently received 1980-83 data. The 1980-83 intake data have been computer-processed, a summary of the data has been issued," and information has been provided on the general type of dietary intake study carried out: (i) composite food groups, in which case the number of food groups is given, (ii) major food items coupled with amounts consumed, and (iii) duplicate portions of meals. Other information includes: total number of food items making up the diet, whether or not beverages have been included, whether the foods were kitchen prepared before analysis, a description (including the weight) of the consumer, the daily consumption of the diet (g/person/day), and the number of diets analysed. In addition, the sampling period is reported. When diet samples were collected over a 2-year period, only the later year is mentioned in this review. Because of the assumptions that have to be made in the designation of a "representative" national diet b The "market basket" of food (also called "total diet") reflects a defined total diet of a consumer for a specific period of time, in proportions based on the available consumption data. c FAO/WHO/UNEP. Summary and assessment ofdata received from the FAO/WHO Collaborating Centres for Food Con- tamination Monitoring. Uppsala, National Food Administration, 1982 (unpublished document). d FAO/WHO/UNEP. Summary of 1980-1981 Monitoring Data received from the Collaborating Centres. Geneva, WHO 1983 (unpublished document). H. G. GORCHEV & C. F. JELINEK tO1 I 'ag D-o c CNCN 0) o nco0co V-(DCM C')'-(00)CN It0) N- 000o 4 C~~~~)c~~~~~~4e-J m 0 ) o0coo %qc M CD ) 0 r-Nt a) It t - 0 U) ° °XNMMC0--4CZ qq- --- V I ~ ~ UIooot0 1C)C4---0 CO C0~~~-: oq?q0° 0o 0o oo 60000 o oo 000 66 t 9V-D r- V- OT- V- 0 0 v-- o1, t C*) o N- - C14 Ioo 000000 I00 0000000000 6o ooooo6 6 66oooooo666 M t-CDOCDN r 0) '- (D(O 00 C')CqNNOO OOq0 ---'-00CN) -00000 0000 ,00000 a 00 66C;666; 666o 6 Z 66 v r' V- q- C00 666 00o Ce-D O CI I10 cn 0 0 M P O : 6 cici c6cM i -- T- cN0 Iii~ ~Io oo-r' - - 0) O r 'tD0CUi O6 0 -tOD °t LO 00 LO CL 0 co U)-O O 1:*c-i6 O C .6 .- OI I. '-e4 -- 0)() C4 q 0)0 -edC4C) LO 0'v- N 4e-tU) Drl-OD0)0 4 Pr-r- -r- 0 r- r0oO Do - c0Oo _ r r- - r- r-b 0co CY 0)0)0)0)C 0)CD) CD e0)0) )0) 0) C) C) 0) 0) C u 0 E 0 0 CD C a co C 0 N 0 z E 0 'O .E cn 948 0 25 4- 0 0) 0) C 0 ._ 0 0. 3: 0 co .C 0( 4) -W ,, C .0 0 0 C 20 0 ea 0) C 0 0 C 2a ._ 0 0 C (D 0 C0 0 C 0 0 10 C 0 20 0 .C C C 0 6.) -C 3 0 .0 .E0' IL E Dx E C .r "O10 C C ._ 0. 0 0 0 0 I-4 .0W 006 C C E E0 0 0 0 C C o o0 0 E E C C 0 0 C C0 000 V c .0 .0 00 W4 W. 0 0 C C .2. E E 00 C C0 0 E EV V 0n 0 . 0 0 EVV .0,W0W0'W 0 00 DIETARY INTAKES OF CHEMICAL CONTAMINANTS and in the selection of the relatively few samples collected per year, data usually must be developed over several years before it can be concluded that a trend has occurred in the intake of a given contaminant. ORGANOCHLORINE PESTICIDES Aldrin and dieldrin (Table 2) A summary of the dietary intake data for aldrin and dieldrin is given in Table 2. Canada showed an appreciable decrease in the intake of residues of aldrin and dieldrin from 1971 to 1977 to a level which is about 22% of the maximum ADI of 0.1 tg/kg body weight. For 1979, Guatemala reported a significantly higher intake in urban than in rural diets. The median intake of aldrin and dieldrin in Guatemala decreased from approximately 90/o to 10%o of the ADI between 1979 and 1984. Between 1979 and 1983, the mean dietary intakes in Japan decreased from 16% to 7% of the ADI. New Zealand submitted medians and 90th percentile data in terms of Lg of contaminant per kg of each of the eight food groups. The daily dietary intake of the contaminant was calculated using published data on the daily consumption of each food group (4). All median values for aldrin and dieldrin in the various food groups were below the limit of detection of 5 Ag/kg. The 90th percentile values of 9 ytg/kg and 7 sg/kg were reported for the dairy products and meat-fish-egg groups, respectively (daily consumption, 520 g/day of dairy products and 321 g/day of meat-fish-eggs). In 1975, at the 90th percentile level, the intake of aldrin and dieldrin residues was equal to the ADI, the main contributors being high fat-containing food groups of animal origin. The lower intake of aldrin/dieldrin in rural areas of Guatemala in comparison to urban areas, could be due to lower consumption of animal products in rural settings. The United Kingdom showed a decrease in the median intake from 20% to 10% of the ADI between 1980 and 1981, but additional data will have to be obtained before it can be determined whether a downward trend is occurring. Between 1974 and 1982, the mean intake in the USA decreased from 45% to 16% of the ADI. In summary, the median dietary intakes of aldrin/dieldrin residues reported by several countries represent a notable percentage of the ADI. In the most recent years, median values range from 5% to 15% of the ADI while mean values range from 7% to 56% of the ADI. In one case, the 90th percentile exceeded the ADI. A decrease of the dietary intakes of residues of aldrin/dieldrin over a period of years may be noted in some countries. Such a decrease might be due to the introduction by some countries of restrictions or bans on the use of these pesticides. DDT complex (Table 3) A maximum ADI of 20 ug/kg body weight has recently been recommended for DDT complex (11). Australia submitted 1980 dietary intake data for six different population groups: women, men, girls, boys, children, and infants. It can be seen that the highest intakes per kg body weight were for children and infants; the mean intake was 5% of the maximum ADI (20 ug/kg body weight) in comparison to 2% of the ADI for adults. An increase in intake per kg of body weight is noticeable with decreasing age groups. Intake of the DDT complex in Canada was low in 1971 (0.8% of the ADI) and decreased further to 0.1I% of the ADI in 1977, perhaps reflecting the decreased use of DDT in that country. A decrease in dietary intake between 1979 and 1984 may be noted in the Guatemala study. For 1978 and 1979, Hungary submitted data on the levels of DDT complex per kg weight of the diet. The diet was characteristic of different population groups: children's home, public catering, old people's home, and boarding school. However, only selected data are presented in Table 3. The intakes per person and per kg body weight were calculated assuming a uniform dietary consumption of 1.9 kg and body weight of 57 kg. Median and 90th percentile dietary intakes averaged, respectively, 1 o and 2% of the ADI during 1978 and 1979. No particular trend can be seen between the intake in different years or for different population groups. Median dietary intakes in Japan remained constant at approximately 0.2% of the ADI between 1979 and 1983. In New Zealand, highest levels of the DDT complex were found in the food groups of animal origin, and of relatively high fat content. The median values were 42 and 18 gg/kg food weight in the meat-fish-egg and the dairy products food groups, respectively. Median values in all other food groups were below the limit of detection of 5 Ag/kg food weight. The total dietary intake (median, 2% of the ADI) represents the maximum likely intake of DDT residues since the diet was not cooked and cooking may decrease the final residues in some foods, and the amount of food consumed is rather on the high side, 3.3 kg (5). In the United Kingdom, intakes reported were less than 1% of the ADI. In the USA, the mean dietary intakes of the DDT complex were low throughout the study period (1972 to 1982) and did not exceed 0.5% of the ADI. The dietary intakes of the DDT complex are low in 949 H. G. GORCHEV & C. F. JELINEK ^^^-a)> 00C'o0roNC')C') to0) r-. 11111 CI (~' N66666 0 ..... C4 o o o C; C; 00CMC - - 0)OM 00r C C4JN4 '--w-C 66666; 00o6o 00i 66666 C- oD c) r- r (D r- (o -t -t cIIIII IP- Nt- - - 0 - 66666660000 CD O It 0 CD I-t0 tID M r CDNN00NOD n CDitD qt o(CNC')MC*) 0O '-0000 NC')'-- -- 00000 C666666 66o66C;6 -6-oo6 66 0 0 M ( b -O I11I1 CVc0 CC OIn ) ' 0 X XCXN _cn 0 N_ CO_ 0C'). C ')C')N N --- _-( N_ ,c O In'- CDr _ CO O CD0 C0 . . . c4 P, cs -t 0 ItI_ - w O a; ai _- VI _- _- _ Pw (N booboo c-N')m r- a O -CN 000000000000 rN-N rs0000 P% N00000 a) )0)0)0 0)0)0) 0)0) ) 0) C a, aCa, E 0 0, C 'C C 3 ._ a, 0 a,'C +. C C aQ (0- ItU Dn CN 00 000000 o6 6666666666 00 1111111100 _q O- _O7 C; 6 00 '- T, 66 66 (DO) 00 0 00 00 CD 0.CO 11eC L 00 O_0 D _0C)CN 0) -CN c') In '-C')unnCDnX _ n- o0- (N Cn O CO - 00 0) N 0C 0C ) -r ) )P )r 0 0Co) CD C) ) m 0) m a) m CD a) _ Un 950 (N(NC')C0)n I 0 0,a, .m 4, _ C 0 - 0, a.a 'a, .0 0)0 ~0 a,0 0, - InO - - I ( 00 0)N. ci 6 6 6 -: - a) C 0 U a 0 0) C m a, 2 a, C 'a0 Q a, C a, U .C 0) m C C 'a C 0 0) a, C C 0 U CD O Go 00 It ON 0 - it0 eDO r- LD0 CXm( £ 0000CD '- InV) MI1 11 0 0 0 00'-0000~N00) 66 66666 66 66oooooooo LI) 4,1 C 0 E 0) C X In a, (N 0o C C-) D~E ._ C In Yq o C00 -a, LI).2 * a, > - ') > Y~ a (N .0 u *4-- I C . 0 b- a >. 0. LO C .0 a,*_om C E 8 .0 00 C C ) ^' . _.O, CQ C 5 0 x COna E ° a m 6 .5C */ 0 CD . . 0,l 0, 0 E x E x a) E 0 0 0 0 C a, a, cvi ID (0 I. CD m CO 951DIETARY INTAKES OF CHEMICAL CONTAMINANTS Table 4. Dietary intakes of hexachlorobenzene (HCB) Intake Intake (ftg/person/day) (ILg/kg body weight/day) Country Year Median Mean 90th percentile Median Mean 90th percentile Canada 1973 5.09 - _ 0.073 - _ 1974 0.82 - - 0.012 - - 1977 0.05 - - 0.001 - - Hungary 19780 3.8 - 7.6 0.067 - 0.133 19790 7.6 - 11.4 0.133 - 0.200 1979b < 0.2 - 1.9 < 0.003 - 0.033 Japan 1979 0.17 0.35 0.96c 0.003 0.007 0.019c 1980 0.08 0.13 0.25 0.002 0.003 0.005 1981 0.11 0.15 0.25 0.002 0.003 0.005 1982 0.04 0.10 0.21 0.001 0.002 0.004 1983 0.11 0.15 0.25 0.002 0.00. 0.005 United Kingdom 1980 0.0 0.14 0.9 0.0 0.002 0.015 1981 0.11 0.31 1.1 0.002 0.005 0.018 USA 1972 - 0.03 - - 0.000 - 1973 - 0.4 - - 0.006 - 1974 - 0.1 - - 0.001 - 1975 - 0.3 - - 0.004 - 1976 - 0.1 - - 0.001 - 1977 - 0.1 - - 0.001 - 1978 - 0.3 - - 0.004 1979 0.2 0.2 0.4 0.003 0.003 0.006 1980 0.211 0.289 0.533 0.003 0.004 0.008 1982 0.109 0.136 0.237 0.002 0.002 0.003 0 Boarding school. b Public catering. Maximum intake. the reporting countries. All 90th percentile values are below 10% of the ADI. Hexachlorobenzene (HCB) (Table 4) Canada showed a steady decrease in the intake of HCB residues beween 1973 and 1977 at which point the median intake was 0.001 gg/kg body weight. Hungary showed a median intake level of 0.07 tg/kg body weight in 1978, and from 0.13 Ag/kg body weight to less than the limit of detection in 1979. Japan showed median intakes of approximately 0.002 jig/kg body weight between 1979 and 1983. Similarly, median intakes of approximately 0.002 jig/kg body weight were reported by the United Kingdom in 1981 and by the USA between 1979 and 1982. No clear trend can be seen in the mean intakes reported by the USA between 1972 and 1982. The data in Table 4 indicate that the median intakes for HCB vary from 0.001 to 0.1 jzg/kg body weight in the diets studied in Canada, Hungary, Japan, United Kingdom, and the USA. The median dietary intakes reported in recent years are in the vicinity of 0.002 dig/kg body weight and show no significant differences between the different countries. The maximum ADI for HCB was 0.6 jg/kg body weight, but it has been withdrawn. Total HCH isomers (Table 5) In Canada, the intake of hexachlorocyclohexane (HCH) isomers decreased from 0.05 Ag/kg body weight in 1971 to 0.01 jg/kg body weight in 1977. The median intakes reported by Guatemala, Hungary, Japan and the United Kingdom were generally around 0.04 jig/kg body weight. In the USA, mean intakes showed an increase from 0.004 to 0.025 jig/kg body weight between 1972 and 1974, at which point a decreasing trend is noticeable down to a value of 0.01 jg/kg body weight in 1982. No ADI has been proposed by the Joint FAO/WHO Meeting on Pesticide Residues for total HCH isomers. Lindane (gamma-HCH) Dietary intake data on lindane residues were submitted by Guatemala, Japan, New Zealand, the United Kingdom, and the USA. All intakes reported, dating back to 1975, constitute a very small percentage (1.2% or less) of the maximum ADI H. G. GORCHEV & C. F. JELINEK Table 5. Dietary intakes of total hexachlorocyclohexane (HCH) isomers Intake Intake (pg/person/day) (pg/kg body weight/day) Country Year Median Mean 90th percentile Median Mean 90th percentile Canada 1971 3.46 - - 0.05 - - 1972 3.34 - - 0.05 - - 1973 2.29 - - 0.03 - - 1974 0.92 - - 0.01 - - 1977 0.70 - - 0.01 - - Guatemala 1979 < 2.4 - - < 0.04 - - 1982 1.2 2.4 7.2 0.02 0.04 0.13 1984 2.3 0.7 2.4 0.04 0.01 0.04 Hungary 1978' 19.0 - 24.7 0.33 - 0.43 1978b 17.1 - 34.2 0.30 - 0.60 1978b 1.9 - 9.5 0.03 - 0.17 1979a 26.6 - 34.2 0.47 - 0.60 1979c 3.8 - 11.4 0.07 - 0.20 1979b < 0.2 - 9.9 < 0.003 - 0.17 1979b 2.7 - 9.5 0.5 - 0.17 1979b 1.1 - 3.0 0.02 - 0.05 1979d 1.3 - 2.5 0.02 - 0.04 Japan 1979 2.2 2.3 3.7' 0.04 0.05 0.07e 1980 1.6 2.0 3.1 0.03 0.04 0.06 1981 2.4 2.9 4.7 0.04 0.06 0.09 1982 1.8 1.8 3.7 0.04 0.04 0.07 1983 2.2 2.6 4.9 0.04 0.05 0.09 United Kingdom 1980 2.6 3.3 8.5 0.04 0.05 0.14 1981 2.2 2.5 5.4 0.04 0.04 0.09 USA 1972 - 0.3 - - 0.004 - 1973 - 0.9 - - 0.013 - 1974 - 1.7 - - 0.025 - 1975 - 1.0 - - 0.014 - 1976 - 1.1 - - 0.016 - 1977 - 1.0 - - 0.014 - 1978 - 0.8 - - 0.011 - 1979 0.8 1.0 1.4 0.011 0.014 0.020 1980 0.852 0.985 1.26 0.012 0.014 0.018 1982 0.75 0.763 1.22 0.011 0.011 0.017 ' Boarding school. b Public catering. c Old people's home. d Children's home. Maximum intake. (10 jug/kg body weight), even at the 90th percentile levels. Heptachlor and heptachlor epoxide Dietary intakes of heptachlor and heptachlor epoxide residues have been received since 1971 from Canada, Guatemala, Japan, and the USA. In every case, the median intakes were 1% or less of the maximum ADI of 0.5 ,g/kg body weight. The highest 90th percentile intakes reported were 9% and 3% of the ADI in Guatemala and Japan, respectively, in 1982. No significant trend is apparent in countries reporting data for several years (Canada, Japan, and the USA). ORGANOPHOSPHORUS PESTICIDES Collection of dietary intake data on diazinon, malathion, parathion and parathion-methyl (Table 6) was initiated in 1980. In all cases the median intake reported for organophosphorus pesticides is low, 1% (or less) of the maximum ADI for the pesticide con- cerned. For countries reporting data over several years (Japan and the USA), a slight increase in intake of organophosphorus pesticides is seen in the more recent years. It will be necessary to obtain data for additional years to determine whether this constitutes a trend. Guatemala reported non-detectable levels for 952 DIETARY INTAKES OF CHEMICAL CONTAMINANTS U) 166o6 66 6666r-~ 66 10000 660 _ ' _ N CON 00 0 0'- 0.0 0 00 oooo 00 0000( 000000'- 00 66666 66 00L00 0000 00 (000 CD000 - C0'- ooo6 66 a666-66 Cr4It 'tC) a 0C O,q_ ) 0) N Ln C')£ 0000 06 m -* r - csN C 00 Ki0N cv) 00' ZZ 0000 1:-N ZZ 666ooo C _CV )LOst r-- V7. . . 00N000 (00 00 9 D01 eDO ZZ 0000 0o- ODN 0o0NWC' 00 NNNC4CNo0 zz 09990 NN ooooo6 6 N 0 nN '-NC')'-0 (0l- 0 9090 C-N ZZ oooo 66 Z Z IOOOOcC4aN 000 "' -( a,0'-NC') ON N a0n-Nc' 00000 000 00 00 r- 0 0 00 00 CC 0 Q.C_A CEr-E .2.c D laCDO CLCU 0 0 Z oooo 00 04C Z0000 0 N (0 0 0 Z 0000 00 v v 0~~~ z oooo 6 0~~~~~0 z 0000 66 0~~ (0 2 oooo ooC v 0C0 0< aZ o 66 00o- Z ooo6 66 00 LOa)a V- 604 Z 0000 66 oN q 0-NCN 0N 00 00 00000 000 a a ,a a 'a C E 0a, < zD CUX0- 4-5 a 4.1~~~~~a 0. 953 C- o0 0 0. ZZ 00 06 V o0 zz00 Na 00 660,CU CD a, C) 0- CU -C .2' CU 4- > .2-0 0 .0 0' 0, *0 0. Z0, ZZ 00 00 v v _ '-- 00 0000D 99 ZZ a 00 V C 0 0. 3 E 0 CD .0 S 0, E> *)V E0, CM ._ - 0E c M 0, *0 0 ._ C- 0 CO X m EU- 04- C Co - CU C' CUC CU C ._' o >- *9 s 0_ CU-D CDUO I-' CU C 0. a, C ._X CU m c _U C 02 CU a, C 2 CUBI U 0. 0 CD mC mC 7E 0 0) a z E m a_ DC 0 0-C 00 zz 00 c0 ZZ oo 0o ZZ oo 040)00 0000 66 '-090 o6 o o (04 00 6oo V V 0 0 zz c0 C CL a, CD .co CUZ C._ xQ a, 0._ -a, CU c Oc wZ 00 _-(0 ZZ oo oo0 v v N N C') o M000 000 000 E :4.. CU co C-I 3 mf cn r-0 0 qqt V-- Cl) Le) qtzz q.q.q.q. .0 19t a a OR C4 co coZ z Io ': . ci 954 H. G. GORCHEV & C. F. JELINEK Table 7. Dietary intakes of polychlorinated biphenyls (PCB) Intake Intake(jtg/person/day) (1tg/kg body weight/day) Country Year Median Mean 90th percentile Median Mean 90th percentile Canada 1977 0.07 - - 0.001 Guatemala 1979 < 4.8 - - < 0.09 - Japan 1979 2.9 - 6.0" 0.06 - 0.12° 1980 2.2 2.3 3.3 0.04 0.05 0.07 1981 2.6 3.1 5.9 0.05 0.06 0.12 1982 1.8 2.3 3.8 0.04 0.05 0.08 1983 2.0 2.6 2.5 0.04 0.05 0.05 United Kingdom 1974 < 15 - - < 0.25 - - 1981 0 0.031 0 0 0.0005 0 USA 1972 - 0.3 - - 0.004 - 1973 - 1.1 - - 0.02 - 1974 - 0.4 - - 0.006 - 1975 - < 0.1 - - < 0.001 - 1976 - < 0.1 - - <0.001 - 1977 - 1.1 - - 0.02 - 1978 - 1.9 - - 0.03 - 1979 0.04 1.0 5.2 0.0006 0.01 0.07 1980 < 0.5 0.523 < 0.5 < 0.007 0.008 < 0.007 1982 < 0.200 0.196 < 0.200 < 0.003 0.003 0.003 a Maximum intake. three of the organophosphorus pesticides: malathion, parathion, and parathion-methyl. POLYCHLORINATED BIPHENYLS (PCB) The data for PCBs in the diets of Canada, Guatemala, Japan, the United Kingdom, and the USA are summarized in Table 7. The mean dietary intakes reported are at or below 0.06 itg/kg body weight. The highest reported intake was 0.12 1g/kg body weight. There is no discernible trend in the reported dietary intakes from 1979 to 1983 in Japan, nor from 1972 to 1982 in the USA. The mean intake in the USA was appreciably higher than the median intake in 1979 indicating perhaps some contamination incidents. A few unusually high findings may have an appreciable effect on the mean level, but little on the median.' Somewhat higher dietary intakes of PCBs were reported from Japan as compared to other reporting countries. This may be due to a higher fish consumption in Japan and the tendency of PCBs to bioaccumulate in aquatic organisms. No provisional tolerable weekly intake has been proposed by the Joint FAO/WHO Meeting on Pesticide Residues for the PCBs. ' See footnote c on page 947. CADMIUM Data on dietary intakes of cadmium (Table 8) were submitted by ten collaborating centres indicating perhaps a general concern about this contaminant. Data from Australia for 1980 and 1981 indicate that the highest intake per kilogram of body weight was for the two-year old child. The nature of the diet of a 9-month infant may preclude against excessive exposure to cadmium. Data gathered in the Food Contamination Monitoring Programme on cadmium levels in individual foodstuffs show that highest levels were found, in a roughly decreasing order, in offal, fish and shellfish, cereals, and vegetables. Sub- stantially lower levels were found in meat and poultry, dairy products, and fruits. the hypothetical diet of a 9-month old in Australia does not include for instance any liver, fish, or fish products in contrast to that of a 2-year old, and contains a lower percentage (by weight) of cereals and vegetables (2). The median intake per kg of body weight is approximately half the PTWI for a 2-year old and about one-fifth the PTWI for an adult. In 1982 and 1983, the intakes for all population groups seem to have decreased. Austria reported in 1978 a median intake of 33% of the PTWI. Canada reported median values of 9007 and 70% of the PTWI in 1971 and 1972, respectively. DIETARY INTAKES OF CHEMICAL CONTAMINANTS 955 Qi x ca 0 0. c 00) 0 0Z Hz XX-S 1 0 0u 0_ c rcs a) N - ' ID_ 0 CD O - OD CD00Ncs _0uL uzO n u o4oVu)CV)NcsX*u o_NNc I a)C' -N_ _ N -N!- NCr 10-DSC9X*C4-CCNNeN--CMC4N CI ICC_r-v- _r- V-1 V-- V-- N w-- N 04oM 4t LCO b-04 CO) qt CD Sv- r- 9- C4c04 Cl It 04 a-r) C N-It 0cob _-- N 4 C) t C4- 4Cl CO) v-- 0 C4 C CM _ _ __ C'4 C) CO CDN CD 0 - - - CD -e o 0 co_ c N0_ )'-NNNoco-)C0N 0-0- C' 0( (N '-'-(Qo0 'o -v 0 00CD - CIO 00Dr00 ( 0 0 t _ C - It rT%t 0 _C 4 It t t ON toO CD 6C CC 9 C 140'-,-'-NC0N0 _____c I I001I_- Icl0Oo_( (_NN00000N 000NO)L010 1N tN (0000)"c'00 v-,tD )10C --NNNIN-UCD NN 0'OD-'-'- N (010 '- 0000C00t-CO' tLO-0 CD c(0001_0NI(D000tM 1-00 rN00C'40CI)C'X) COCY) (OC1cMc'coo N M -t M 10, M,-t it~ ~ ~ ~ ~ ~ ~ ~ ~C 0 M o unT- ) w r-(0N0 C r- C0 0000 W 0 N ItCD Cf) r- OD00CV)04 C4N000 C 0 M t n C P% C0C N r N O CD0- tD 0- v-0,NN 1 N N IN ( N- DN-NC')0 N ____MMWM-014*0r-qtOWN,tLOC')COOOCDOOc,4C' U)r-CN ____ ____ uc4u) o 4 Q s B ~ ~ ~ ~ ".4 "v v -, o @ -gcb '-'-'a-'- NvNN v' v0 -N 0000N 000 -N MMW 000000000000000000000000 r- 0000 -r-. 000000 > 000000000000000000000000 0 00 0000 00 00000000V- r. ,r.- -1- - - - w- I" -v-, --V -- - -' - -v,V- w-- w- - - - V- I.- V r -' - -' . n E >. c la a) Co 4-+a, c ns cm < u tD I CU 0) 0) 0) 0) Ca) 0) C.c C.) 0) CL 0) 0) a) a) 0) CL 0) a) D ._a) (D C ._ 0C 0_ a) CD a) 0 .0 -O 0) Cl .m CY) a- 0C 0) -C 0 3 ._ 0 -o C._ (Cl Q a- 0_ 0 C 0 0c 0 * CU m'U C') 0 H. G. GORCHEV & C. F. JELINEK - 0eN C*) C0Nwo0 cODCOr%CO rU 0 00(00 COwIn) Ir C) 1010 r- O 0)co )c_n Lo COv--_ P PCEe C4 N C E) CO ) CE E)m m oI* COD--N i0 LCO CO LO OD r-.. P. 00100L-O _ N4NNNNNClNCl r-.Or- 0 LoW0 ai0)0010(010 C')Cl4 7 " 0Lo0r-EC') LO ')0 u LO 0 C')LO v- 0 OD00'- - CD D lC')q Mr%l- - O On6 4 .44 IQiCjej eC'a )Cl >CiC4 C l . . . . ....... o Lo00C'4I00) v- N -0))-r-- N- cOCOc a 0o_cc-t,COLn*C') C') l l0 - l C0.0. co14Cl0)La104C' Cl 0)'-0'0)0 6qL O- c4 o I ro co00 r^ci 6CE r-.t CV) m m N _- N_ __~- w- 04 C'O LOC''CIOC ')N C')0C4C 0) C') -:'0 _a- OOCOOM000CE)ClN _ ___________ N C4 N 0)0-C lCE) ~- ClS1 O -Cl E) )~ C Orb0O0)0b c0W- C4 M 0 V- 4 'R Lo 0 N 00 0 1- N M V- q M -4 Lo 0 P' 00 C4 r-..0oOooOD P% OD -P% %P%r-rocnoW Oo r"-r-I %r- % o'oM0) 0)CD0)0) ) D 0) 000)C) D 0 0)0 0)0 0) 0)0CD0)0CD0) 0) vC 0 V0N 0 z C e 0 C,, E 0 ._0) .0CE .2).-C 0 0 .0 cm IC 0 CO s0 tmD C *E E >x o c . N O) cO C o E ' ° D°0 CV .0 0 W.F.I ° c 4.ECC 2 o o vDt > aE-E 0'¢y a-10 C.) Lf WOoDC lI 2t o Y @> -0E E D 01 0 o Co e 4 .9 * *'-0 _ _0C_ C C 0. _-_ tl "P 0.0 0)) C'i 0 0 0)0C)0 0 ).0 1 0 o 2 0C co.°0'E10 *K3o C0O C0 e0)_> .0 a-. C= C >' OD W0 ) ,. OCD) 0 0c0 0cco co( rE r- E a- * 956 0 0 1- C b- CL :2 0 ._. 0e 0 0 C. 0 0 C 0 0 0 ._ D C 0 o 0 0) C co 0 0 -W C 0 0 0 C. 0 U 0 C01 0 C 0 0 0 0 C 0 U 'b q) .0 I... C a 0 DIETARY INTAKES OF CHEMICAL CONTAMINANTS Guatemala reported the mean intakes in 1979 for low-income rural and urban areas. The intake was higher in the rural area. Intake levels for the urban areas were lower in 1982 and 1984 than in 1979. However, further data will have to be obtained to determine whether these trends are significant. Hungary submitted in 1978 and 1979 data for a variety of diets, e.g., a boarding school (seasonal samples) and public catering places, and in 1980-83 for diets of various population groups of different ages, sex and body weight. A partial listing of these intake values is given in Table 8. A comparison of the median values for different population groups show higher intakes for children than for adults. In Japan, median dietary intakes ranged from 50% to 80% of the PTWI. They decreased between 1979 and 1983 but additional data would need to be obtained to ascertain whether a downward trend is occurring. New Zealand and Sweden reported median/mean intakes of approximately 15% of the PTWI in 1975 and 1980 respectively. The 90th percentile value for New Zealand is based on the sum of the 90th percentile values of the individual composites instead of the diet samples. Such a value is expected to be largely exaggerated and should not be considered as a reflection of the real situation. The United Kingdom reported median intakes of approximately 250o of the PTWI between 1971 and 1983. Median intakes in the USA were approximately 37% of the PTWI between 1979 and 1982. The mean intakes between 1971 and 1982 averaged about 45% of the PTWI, with no real trend apparent. In all the reporting countries, the median cadmium dietary intakes constitute an appreciable percentage of the PTWI. At the 90th percentile intake levels, the PTWI was exceeded in some cases. Exposure to cadmium in the diet is of public health concern. Such exposure should continue to be monitored and appropriate measures taken to minimize its occurrence. LEAD All eleven collaborating centres submitted data on dietary intakes of lead and these are given in Table 9. Australia reported the highest intakes per kilogramme of body weight for the 9-month old infant; the median values amounted to 60070 and 30% of the PTWI in 1980 and 1983, respectively. At the 90th percentile levels, the intakes for the 9-month old exceeded the PTWI in 1980 and 1981. The hypo- thetical diet of a 9-month old includes a relatively high amount of canned foods (2) which are known to be a major source of dietary lead. It should be noted that the PTWI for lead is not applicable to infants and children (12). Between 1980 and 1983, the median intakes for adults and adolescents were generally around 10-20% of the PTWI. Austria reported a median intake of 11% of the PTWI in 1978. Canada reported a decrease in median intake from 30% to 15% of the PTWI in 1971 and 1972, respectively. Ireland reported a mean intake of 35% of the PTWI in 1982. In Guatemala, the mean intakes reported for low- income rural and urban areas from duplicate diet samples in 1979 were around 46-49 isg/kg body weight which is very close to the PTWI of 50 Ag/kg body weight. The mean dietary intake reported for 1982 and 1984 were appreciably less although the population groups studied were not strictly comparable. Further data must be obtained to assess the significance of the decrease in intake reported for 1982 and 1984. Hungary reported dietary intake data every year from 1978 to 1983 for a variety of population groups. No particular trend can be seen between various population groups. The average of the median values reported in different years are: 15% of the PTWI in 1978, 25% in 1979, 22% in 1980, 27% in 1981, and 20% of the PTWI in 1982 and 1983. A partial listing of these data is given in Table 9. In 1983, the intakes per kg of body weight increased with decreasing age and exceeded the PTWI for the 3-6-year age group. Japan reported median dietary intakes of 11-23/o of the PTWI between 1979 and 1983. New Zealand reported a median intake of 521o of the PTWI in 1979. The high intake reported by New Zealand is partly due to the greater average weight of the diet used in their studies. It is of interest to note that about 4007 of the lead intake from this diet was supplied from the canned food composite. Mean intakes in Sweden during 1980 were 5% of the PTWI. A decreasing trend may be seen in median intakes in the United Kingdom between 1971 and 1983. Mean intakes in the USA were in the range of 15% of the PTWI between 1973 and 1982. AFLATOXINS Only Guatemala submitted data on dietary intakes of total aflatoxins. In 1979, these were not detected in diet samples. In 1982 and 1984, the mean and 90th percentile intakes were, respectively, about 0.2 and 0.5 ,g/kg body weight. The detection limit was 4 1g/kg sample and a value of half the detection limit (2 ,g/kg) was used to calculate the mean when aflatoxins were not detected. Aflatoxins B1 and B2 were not detected in the 1982 diet samples in Japan. 957 H. G. GORCHEV & C. F. JELINEK OD -O D0 DXOXr N DXa mc )Sb o CD0 C0) r a- C0 rO CD c r-110 N '-M r- r- - -t r- M N 0 N ur Nr- 0- _) I C400 C N 0 0 0C' o0 C )C) 0c r (t 0 um CD 0 t - 0 P 0 - O o 0 _ o U) NC0) 0)0 0o 'I r 0 v- N NC,)CD - -- -N4 C,O ---N lq IR v- C- - M _- qt M -CX ---w-'t-N -t N Or'~~O0C00)LDU)L0~~r~ -00 0C00tW)r-.-C0r% o~~6~~co~~0)eic', ~~oi II 16( 41460iC~0660 _- N N M It rl _- _- _ N N U) _- _- _- C1 qt _- C4 C1 C1 w--- C14W. -- M o0 W0- It MM MM W W0 XO- 0MM MN r- N b-0 0:MN 6 . . . . . .~. .- . . . .~. . . .~. . . . .6 T--V-v-V. C1 q - V- C- C4 T- T- N 04v" C0 )'- CO 000e0 uio6.-0I I r- o ic.'iC 't It C4 - w- C14 q- NCO 1flC0-0 0 CD ) aD O- ) I aoVoC% 0 0) C CO L010)CN0-.0 __c __-N NN T- _- C1 N CND 0000)DSOO,00rrNC-O-'OO tD0)n l- --LOCOC00 00r0C Ue LLO-C0) 0 0C')-14C 00) 0)LO101- ' tI 1o 0r%mn00) 00MoV-- M 1C- ')(M0 N0co N 0.(N o N CDoII)000'CN _- C# C# -- - -1 I- - - C4 C,)V-0 lq C_ cn qt O O ) T_ C4 0 0 co CN 0 C-4 -tN 00 LO W r m in co co r - o)00) It o co N (0 CD C nt Ln - LDCO m m co CD0 0 cn m C1 t C4 4 LO r II N r- N _- _CO _0 000000---_--bI MNFIC,)CNOC)C 0 -4 0 00 00 _ 0 00 0 0)00)00 00)00 ) )0)w0o0)00000oo) 0) 0)0 0r0)0) )0)0)0)0)0)000a)0Oo)00O00000000owaw0000~~~0 0 MO) Ma0o0 mmc)0mmmC)a CU3 C-al1 cU as as M E IC CU co coCU C I3 958 . .) m t 0 0C 4- CUC Ca) 02 a - 4Q 4- C C. CO 0 0) CU .C Q 4-; z 0 .0 C CO .0 4) 40 .0 C 0 0 '- c0 0) CU ._ ._ C. CD 0 0 0._ CU .a) 0. a1) C .) .C a)0) C a) C C 0 0) aC5CU V S .q_- .C C a .C C a) C 5 CU 5 C 0 0 DIETARY INTAKES OF CHEMICAL CONTAMINANTS O> N r- m ' U.) O r- r- qt U, cOD N NJ 0I C) -t _ _ N> N- UIn0cU" OI "I --aJC J" D IU'NCN_-_ N Moc---00U' --------- IDCV)0IDCU)0 N0e0 £ _N0)_ID r CN ____ _ co r -- oI o 0 C) U) I I I 00V--- I0Noo0COI_O0> eD O PN0 ai 0 0 ui 1-CNi )N-C' C 4 mm IDCMW0)CD'- Pr. 6 6D ( 1(ID,1- aZ co I oi rz -~rz v- cNq 1 -v 0 ILODr- r- i-- c o IL II Pnt0u w CD l llb- N000(0(0w o- le ONooo 66-e-om N- CN-4 -.0 _ % 11111 IcrICOc6O(00o aiuN.)CO cO _- 00 SIl LO1t N0 N040CO C D a) cD r- Or-o oou 0) ID1t CO (0c c(N4 0 V- r M W V- qt M 0 V- Ci C ORI_tNCrorD r-owco c0 V" 1-1 t- r- In (N )o0_cNC 0) o _c4 CD00 '-C' ON-C00 C4 00 N-OD00DOD N- OD N- N--r Nr-N-C00D00 N- -N-N-N-r-r0000 0000))O 0 0)0000)0) 00)0)0)0)0)0) c a, N 3a z c CDa, E 0 cm ._G .P_ 0, U~) 959 @3a; C ._M E Exa, 6cvi6 Cci~ r.zI I. . . . O) CD U) -Q0 0) r PN -O6 PeD( ai c a,t 0E. a, 0,O a,.D C>a, 0 I.ECm - 3 -.5 07 ,0 0L c 0a1 .c U 0) 0) C co a, a, C 2 0 .a 0 a, 0 a) C a, a, C a, 0) C a, a, C 0 Ulo N- co co 40 N- cON-0)0CDcN N- N '- 0)a .) Q) k la H. G. GORCHEV & C. F. JELINEK The Joint FAO/WHO meeting on Pesticide Residues has not proposed a provisional tolerable weekly intake for aflatoxins. CONCLUSIONS Dietary intake data of selected pesticides, PCBs, cadmium, lead and aflatoxins have been collected under the Food Contamination Monitoring Programme. Nearly all data collected so far are from developed countries. In many of these developed countries, certain uses of these pesticides and PCBs have been curtailed or prohibited. There is a need to collect additional dietary intake data from developing countries where some of these pesticides are known to be used extensively. Such data would provide better global coverage and a better assessment of the magnitude of exposure to contaminants in the diet. Dietary intake data indicate that in some countries the exposure to certain organochlorine pesticides (aldrin and dieldrin) may constitute a significant portion of the ADI. As would be expected, higher levels of fat-soluble organochlorine compounds were found in the animal fat-containing portions of the diet such as meat, fish, poultry and dairy products. An increase in intake of animal fats may result in higher dietary exposure to organochlorine compounds. The dietary intakes of residues of organo- phosphorus pesticides where reported, are low in all cases. A slight increase may be noticeable in some reporting countries, perhaps reflecting a trend towards replacing organochlorine with organo- phosphorus pesticides. Dietary intakes of cadmium and lead as reported by eleven collaborating centres constitute an appreciable percentage of the PTWIs for these two contaminants. Dietary intakes of cadmium and lead per kg body weight are highest for infants and young children who are considered to be the susceptible groups and are at highest risk for lead. Every effort should be made to reduce the levels of cadmium and lead in food and drinking-water. There may be an upward trend in the dietary intakes of some contaminants in certain countries in the more recent years. Where such a trend is occurring, the countries concerned should be particularly vigilant in monitoring the dietary intakes of these contaminants and in taking appropriate measures to reverse such an upward trend. Comparison between the reported levels of exposure to certain contaminants (HCH isomers, HCB, PCBs, aflatoxins) and permissible exposure levels cannot be made because of the absence of defined FAO/WHO toxicologically acceptable/ tolerable intake levels. ACKNOWLEDGEMENT Special thanks are extended to the eleven Joint FAO/WHO Collaborating Centres for Food Contamination Monitoring (see Annex 1) whose cooperation has made the compilation of this report possible. RtSUMt EXAMEN DES DOSES DE CONTAMINANTS CHIMIQUES ABSORBtES AVEC LES ALIMENTS Rassembler les donnees sur les contaminants alimentaires est une initiative relativement recente du Programme mixte FAO/OMS de surveillance de la contamination des produits alimentaires. En 1979, les centres collaborateurs FAO/OMS pour la surveillance de la contamination des produits alimentaires ont commence a communiquer des donnees sur les doses de certains contaminants chimiques presents dans l'alimentation et a fournir certains details sur la fagon dont les doses absorbees avec les aliments (doses alimentaires) etaient determin6es. Presque toutes les donnees recueillies jusqu'a present proviennent de pays developpes. De ces derniers, nombreux sont ceux dans lesquels certains emplois de pesticides et de polychlorobiphenyles (PCB) ont e limites ou interdits. Il est necessaire de recueillir davantage d'informations des pays en developpe- ment oii l'emploi de certains de ces pesticides est tres repandu. Ces informations permettraient de mieux connaltre la situation mondiale et l'ampleur de l'exposition aux contaminants presents dans les aliments. Des informations ont e obtenues sur les doses quotidiennes estimees des contaminants retenus pour etre surveill6s par le Programme, a savoir I'aldrine et la dieldrine, le DDT et ses derives, I'hexachlorobenzene (HCB), 1'ensemble des isomeres de l'hexachlorocyclohexane (HCH), le lindane (gamma-HCH), I'heptachlore et l'heptachlore sous forme d'epoxyde, le diazinon, le malathion, le parathion, le parathion-methyl, les polychlorobiphenyles, les aflatoxines, le cadmium et le plomb. Les informations concernant ces contaminants alimentaires ont e fournies par les centres collaborateurs 960 DIETARY INTAKES OF CHEMICAL CONTAMINANTS d'Australie, d'Autriche, du Canada, des Etats-Unis d'Amerique, du Guatemala, de Hongrie, d'Irlande, du Japon, de Nouvelle-Zelande, du Royaume-Uni et de Suede. L'Autriche, l'Irlande et la Suede n'ont fourni d'infor- mations que sur le cadmium et/ou le plomb. Tres peu de donnees concernant les aflatoxines ont ete reques. Les donnees reques couvrent la periode 1971-1983. Pour determiner les problemes de sante que pouvait creer la presence de contaminants toxiques dans les aliments, on a cherche A savoir si les doses alimentaires reelles appro- chaient ou depassaient la dose journaliere admissible (DJA) ou la dose hebdomadaire admissible temporaire (DHAT). Une comparaison entre les niveaux d'exposition A certains contaminants (isomeres de l'HCH, HCB, PCB, aflatoxines) et les niveaux d'exposition admis n'a pas ete possible du fait de l'absence de fixation par la FAO/OMS de doses admis- sibles/tolerables sur le plan toxicologique. Les caracteristiques de l'alimentation et les preparations utilis&es pour l'analyse varient considerablement d'un pays A l'autre, et la methode employ&e dans un pays donne depend des ressources disponibles, des habitudes alimen- taires locales et des types de consommation. Certains pays ont donne des chiffres concernant differents groupes de population. Par exemple, les donnees provenant d'Australie concernaient les nourrissons de 9 mois (poids moyen 9,5 kg), les enfants de deux ans (12,25 kg), les femmes (58 kg), etc. La Hongrie a fourni des informations concernant divers groupes de consommateurs d'age et de sexe differents (eleves internef, pensionnaires de maisons de retraite). A partir des ehiffres indiques en jig/personne par jour, les doses alimentaires correspon- dantes ont ete calculees dans chaque cas par kilogramme de poids corporel. Les valeurs medianes des doses alimentaires de residus d'aldrine/dieldrine signalees par plusieurs pays representent un pourcentage notable de la DJA. Ces dernieres annees, les valeurs medianes allaient de 5 A 15%o de la DJA alors que les valeurs moyennes allaient de 7 A 56% de la DJA. Dans un cas, la valeur au 90eme centile depassait la DJA. Une diminution des doses alimentaires de residus d'aldrine/ dieldrine a ete observee sur quelques annees dans certains pays. Cette diminution peut etre due A la decision prise par certains pays de limiter ou d'interdire l'emploi de ces pesticides. Les doses alimentaires de DDT et de ses derives sont assez basses dans les pays qui ont communique des donnees. Toutes les valeurs au 90eme centile sont inferieures A 10% de la DJA. Les doses medianes pour le HCB varient de 0,001 A 0,1 jg/kg de poids corporel dans les etudes alimentaires faites au Canada, aux Etats-Unis, en Hongrie, au Japon et au Royaume-Uni. Ces dernieres annees, les doses alimentaires medianes signalees avoisinaient 0,002 jg/kg de poids corporel et il ne semble pas y avoir de difference importante entre les differents pays. Les doses medianes de HCH total signalees par le Guatemala, la Hongrie, le Japon et le Royaume-Uni avoisi- naient en general 0,04 fig/kg de poids corporel. Toutes les informations concernant les doses de lindane (gamma-HCH) n'indiquaient qu'un tres petit pourcentage (1,2%o ou moins) de la DJA maximale (10 jig/kg de poids corporel), meme au 90eme centile. Les doses alimentaires medianes des residus d'hepta- chlore et d'heptachlore sous forme d'epoxyde representent 1% ou moins de la DJA maximale de 0,5 jig/kg de poids corporel. En 1982, au Guatemala et au Japon, on a observe les doses les plus elevees au 90eme centile, avec respecti- vement 9 et 3% de la DJA. Comme prevu, les donnees sur les doses alimentaires montrent que les concentrations les plus elevees d'organo- chlores liposolubles sont trouvees dans les aliments contenant des corps gras d'origine animale tels que la viande, le poisson, les volailles et les produits laitiers. A une augmentation de l'ingestion de corps gras d'origine animale peut correspondre une plus grande exposition alimentaire aux organochlores. La collecte de donnees sur les doses alimentaires concernant le diazinon, le malathion, le parathion et le parathion-methyl a commence en 1980-1981. Dans tous les cas, la dose mediane signalee pour les pesticides organo- phosphores est basse-1% ou moins de la DJA maximale pour le pesticide indique. Dans certains pays, une discrete augmentation a et notee qui reflete peut-etre une tendance A remplacer les pesticides organochlores par des produits organophosphores. Des informations concernant les PCB dans les aliments ont ete recues du Canada, des Etats-Unis d'Amerique, du Guatemala, du Japon et du Royaume-Uni. Les doses alimentaires moyennes sont inferieures ou egales A 0,06 jg/kg de poids corporel. La dose la plus forte qui a ete signalee etait de 0,12 jig/kg de poids corporel. Les informations provenant du Japon montrent que les doses alimentaires de PCB y sont quelque peu plus elevees que dans les autres pays. Ceci est peut-etre du A une plus forte consommation de poisson et A la tendance des PCB a s'accumuler dans les organismes aquatiques. Des donnees sur les doses alimentaires de cadmium ont ete fournies par dix centres collaborateurs. En Australie, la dose la plus elevee par kg de poids corporel a ete observee chez les enfants de deux ans. Dans tous les pays, les doses alimentaires medianes de cadmium representent un pour- centage appreciable de la DHAT qui, dans certains cas, etait depassee au niveau du 90eme centile. L'exposition au cadmium par l'alimentation pose un probleme de sante publique. Cette exposition doit continuer A etre surveillee et les mesures appropriees doivent etre prises pour en diminuer la frequence autant que possible. Les onze centres collaborateurs ont fourni des donnees sur les doses alimentaires de plomb, contaminant qui semblait poser partout un certain probleme. Plusieurs groupes de population ont ete etudies en Australie; la plus forte dose de plomb absorbee par kilogramme de poids corporel etait observee chez les nourrissons de 9 mois. Les doses alimentaires de plomb signalees par plusieurs pays representaient un pourcentage appreciable de la DHAT pour ce contaminant. Les nourrissons et les jeunes enfants sont consideres comme etant les groupes les plus sensibles et courant les risques les plus eleves. Tout devrait etre entrepris pour reduire les teneurs en plomb des aliments et de l'eau de boisson. 961 962 H. G. GORCHEV & C. F. JELINEK REFERENCES 1. WHO Technical Report Series, No. 592, 1976 (Pesticide residues infood: report of the 1975 Joint Meeting of the FAO Working Party of Experts on Pesticide Residues and the WHO Expert Committee on Pesticide Residues), p. 39. 2. AUSTRALIAN NATIONAL HEALTH AND MEDICAL RESEARCH COUNCIL. Market basket (noxious substances) survey of foods, 1982. Canberra, Australian Government Publishing Service, 1982. 3. SMITH, D. C. ET AL. Pesticide residues in the total diet in Canada. IV. 1972 and 1973. Pesticide science, 6: 75 (1975). 4. DICK, G. L. ET AL. Survey of trace elements and pesticide residues in the New Zealand diet. 1. Trace element content. New Zealandjournal ofscience, 21: 57 (1978). 5. DICK, G. L. ET AL. Survey of trace elements and pesticide residue content. 2. Organochlorine and organophosphorus pesticide residue content. New Zealandjournal ofscience, 21: 71 (1978). 6. SLORACH, S. EL AL. Intake of lead, cadmium and certain other metals via a typical Swedish weekly diet. Vdr FOda, 35 (Suppl. 1): 1-16 (1983). 7. MINISTRY OF AGRICULTURE, FISHERIES AND FOOD. Report of the Working Party on Pesticide Residues (1977-1981), Food Surveillance Paper No. 9 (1982); Survey of lead in food: second supplementary report, Food Surveillance Paper No. 10 (1982); Survey of cadmium in food: first supplementary report, Food Surveillance Paper No. 12 (1983). London, Her Majesty's Stationery Office, 1982, 1983. 8. PENNINGTON, J. A. T. Revision of the total diet study food list and diets. Journal of the American Dietetic Association, 82: 166-173 (1983). 9. DUGGAN, R. E. ET AL, Residue monitoring data. Pesticide residue levels in foods in the United States from July 1, 1969 to June 30, 1976. Washington, DC, Food and Drug Administration and Association of Official Analytical Chemists, 1983. 10. GLOBAL ENVIRONMENTAL MONITORING SYSTEM. Guide- lines for the study of dietary intakes of chemical contaminants. Geneva, World Health Organization, 1985 (Offset Publication No. 87). 11. Pesticide residues in food- 1984 evaluations. Report sponsored jointly by FAO and WHO. (FAO Plant Production and Protection Paper 62). Rome, Food and Agriculture Organization, 1985. 12. WHO Technical Report Series, No. 505, 1972 (Evaluation of certain food additives and the contaminants: mercury, lead, and cadmium: sixteenth report of the Joint FAO/WHO Expert Committee on Food Additives). Annex I PARTICIPANTS IN FAO/WHO FOOD CONTAMINATION MONITORING PROGRAMME Australia Mr S. W. C. Smith, Food Administration Section, Department of Health, Canberra, A.C.T. Austria Dr. J. Ettl, Ministry of Health and Environmental Protection, Vienna. Canada Dr H. B. S. Conacher, Food Research Division, Health Protection Branch, Department of National Health and Welfare, Ottawa. Guatemala Ing. (Mrs) Marit de Campos, Unified Food and Drug Control Laboratory (LUCAM), Guatemala City. Hungary Dr V. Cieleszky, Department of Toxicological Chemistry, Institute of Nutrition, Budapest. Japan Dr M. Uchiyama, Division of Food, National Institute of Hygienic Sciences, Tokyo. Ireland Dr T. O'Toole, Department of Agriculture, Agriculture House, Dublin. New Zealand Mr J. Fraser, Division of Public Health, Department of Health, Wellington. Sweden Dr S. A. Slorach, Toxicology Laboratory, National Food Administration, Uppsala. United Kingdom Dr P. J. Bunyan, Food Science Division, Ministry of Agriculture, Fisheries and Food, London. United States of America Dr C. F. Jelinek, Bureau of Foods, Food and Drug Administration, Department of Health and Human Services, Washington, DC.