Many wildlife species may be exposed to biologically active concentrations of endocrine-disrupting chemicals. There is strong evidence obtained from laboratory studies showing the potential of several environmental chemicals to cause endocrine disruption at environmentally realistic exposure levels. In wildlife populations, associations have been reported between reproductive and developmental effects and endocrine-disrupting chemicals. In the aquatic environment, effects have been observed in mammals, birds, reptiles, fish, and mollusks from Europe, North America, and other areas. The observed abnormalities vary from subtle changes to permanent alterations, including disturbed sex differentiation with feminized or masculinized sex organs, changed sexual behavior, and altered immune function. For most reported effects in wildlife, however, the evidence for a causal link with endocrine disruption is weak or nonexisting. Crucial in establishing causal evidence for chemical-induced wildlife effects appeared semifield or laboratory studies using the wildlife species of concern. Impaired reproduction and development causally linked to endocrine-disrupting chemicals are well documented in a number of species and have resulted in local or regional population changes. These include: Masculinization (imposex) in female marine snails by tributyltin, a biocide used in antifouling paints, is probably the clearest case of endocrine disruption caused by an environmental chemical. The dogwhelk is particularly sensitive, and imposex has resulted in decline or extinction of local populations worldwide, including coastal areas all over Europe and the open North Sea. DDE-induced egg-shell thinning in birds has caused severe population declines in a number of raptor species in Europe and North America. Endocrine-disrupting chemicals have adversely affected a variety of fish species. In the vicinity of certain sources (e.g., effluents of water treatment plants) and in the most contaminated areas is this exposure causally linked with the effects on reproductive organs that could have implications for fish populations. However, there is also a more widespread occurrence of endocrine disruption in fish in the U.K., where estrogenic effects have been demonstrated in freshwater systems, in estuaries, and in coastal areas. In mammals, the best evidence comes from the-field studies on Baltic gray and ringed seals, and from the Dutch semifield studies on harbor seals, where both reproduction and immune functions have been impaired by PCBs in the food chain. Reproduction effects resulted in population declines, whereas impaired immune function has likely contributed to the mass mortalities due to morbillivirus infections. Distorted sex organ development and function in alligators has been related to a major pesticide spill into a lake in Florida, U.S.A. The observed estrogenic/antiandrogenic effects in this reptile have been causally linked in experimental studies with alligator eggs to the DDT complex. Although most observed effects currentl...

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Contents of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and of 16 further congeners--polychlorinated dibenzodioxins and dibenzofuranes (PCDD/PCDF)--were determined in lipids of adipose tissue and of livers of 3 stillborns and of 17 infants (0.43-44 weeks old) who died from sudden infant death syndrome. International toxic equivalents (I-TEq) calculated for the sum of TCDD together with all of the 16 congeners (1.55-29.63 ng/kg lipids of adipose tissue, n = 20; 2.05-57.73 ng/kg liver lipids, n = 19) were within the range of or lower than the values published for adults. TCDD concentrations in lipids of breast-fed infants were higher (0.38-4.1 ng/kg lipids of adipose tissue, n = 9; 0.49-3.9 ng/kg liver lipids, n = 8) compared to non breast-fed subjects (0.16-0.76 ng/kg lipids of adipose tissue, n = 8; 0.29-0.71 ng/kg liver lipids, n = 7). Neither I-TEq values nor TCDD concentrations exceeded values published for adults. Since even in stillborns PCDD/PCPF were found (I-TEq, 9.70-10.83 ng/kg lipids of adipose tissue, 6.17-8.83 ng/kg liver lipids; TCDD, 1.3-2.1 ng/kg lipids of adipose tissue, 0.76-1.5 ng/kg liver lipids; n = 3), transplacental exposure has to be deduced. All of the findings concerning TCDD concentrations in the organism become intelligible on the basis of a physiological toxicokinetic model which was developed to describe the body burden of TCDD for the entire human lifetime in dependence of TCDD uptake from contaminated nutrition. The model reflects sex and age dependent changes in the following parameters: body weight, volumes of liver, adipose and muscle tissue, food consumption, and excretion of faeces. TCDD is supposed to be taken up orally, to be distributed freely in lipids of the organism and to be eliminated unchanged by excretion in lipids of faeces as well as by metabolism in the liver. The model was used to predict the half-life of elimination of TCDD (4 months in newborns increasing to approximately 5 years in adults) and concentrations of this compound in lipids of adipose tissue, blood, liver and faeces at different ages. Furthermore, the influence of breast-feeding on the TCDD burden of a mother, her milk and her child was simulated. The model was validated by means of own data gained in adipose tissue and livers of infants and also using a series of values measured by other authors in mother's milk and in tissues and faeces of infants and adults. Predictions as well as experimental findings demonstrate a distinct increase in the TCDD body burden of breast-fed infants. Generally, it can be concluded for the excretion of unchanged, non-volatile, non protein bound highly lipophilic compounds that their half-life is short in infants (approximately 5 months) and increases to approximately 10 years reached between 40 and 60 years of age.

Chinese hamster V79 cell lines were constructed for stable expression of human cytochrome P450 1B1 (P450 1B1) in order to study its role in the metabolic activation of chemicals and toxicological consequences. The new V79 cell lines were applied to studies on DNA adduct formation of the polycyclic aromatic hydrocarbon (PAH) dibenzo[a,l]pyrene (DB[a,l]P). This compound has been found to be an environmental pollutant, and in rodent bioassays it is the most carcinogenic PAH yet discovered. Activation of DB[a,l]P in various metabolizing systems occurs via fjord region DB[a,l]P-11, 12-dihydrodiol 13,14-epoxides (DB[a,l]PDE): we found that DB[a,l]P is stereoselectively metabolized in human mammary carcinoma MCF-7 cells to the (-)-anti- and (+)-syn-DB[a,l]PDE which both bind extensively to cellular DNA. To follow up this study and to relate specific DNA adducts to activation by individual P450 isoforms, the newly established V79 cells stably expressing human P450 1B1 were compared with those expressing human P450 1A1. DNA adduct formation in both V79 cell lines differed distinctively after incubation with DB[a,l]P or its enantiomeric 11,12-dihydrodiols. Human P450 1A1 catalyzed the formation of DB[a,l]PDE-DNA adducts as well as several highly polar DNA adducts as yet unidentified. The proportion of these highly polar adducts to DB[a,l]PDE adducts was dependent upon both the concentration of DB[a,l]P and the time of exposure. In contrast, V79 cells stably expressing human P450 1B1 generated exclusively DB[a,l]PDE-DNA adducts. Differences in the total level of DNA binding were also observed. Exposure to 0.1 microM DB[a,l]P for 6 h caused a significantly higher level of DNA adducts in V79 cells stably expressing human P450 1B1 (370 pmol/mg of DNA) compared to those with human P450 1A1 (35 pmol/mg of DNA). A 4-fold higher extent of DNA binding was catalyzed by human P450 1B1 (506 pmol/mg of DNA) compared to human P450 1A1 (130 pmol/mg of DNA) 6 h after treatment with 0.05 microM (-)-(11R,12R)-dihydrodiol. In cells stably expressing human P450 1B1 the DNA adducts were derived exclusively from the (-)-anti-DB[a,l]PDE. These results indicate that human P450 1B1 and P450 1A1 differ in their regio- and stereochemical selectivity of activation of DB[a,l]P with P450 1B1 forming a higher proportion of the highly carcinogenic (-)-anti-(11R, 12S,13S,14R)-DB[a,l]PDE metabolite.