2,3,7,8-Tetrachlorodibenzo-p-dioxin inhibits steroidogenesis in the rat testis by inhibiting the mobilization of cholesterol to cytochrome P450scc

Threshold of toxicological concern for chemical substances present in the diet: a practical tool for assessing the need for toxicity testing

The de minimis concept acknowledges a human exposure threshold value for chemicals below which there is no significant risk to human health. It is the underlying principle for the US Food and Drug Administration (FDA) regulation on substances used in food-contact articles. Further to this, the principle of Threshold of Toxicological Concern (TTC) has been developed and is now used by the Joint FAO/WHO Expert Committee on Food Additives (JECFA) in their evaluations. Establishing an accepted TTC would benefit consumers, industry and regulators, since it would preclude extensive toxicity evaluations when human intakes are below such threshold, and direct considerable time and cost resources towards testing substances with the highest potential risk to human health. It was questioned, however, whether specific endpoints that may potentially give rise to low-dose effects would be covered by such threshold. In this review, the possibility of defining a TTC for chemical substances present in the diet was examined for general toxicity endpoints (including carcinogenicity), as well as for specific endpoints, namely neurotoxicity and developmental neurotoxicity, immunotoxicity and developmental toxicity. For each of these endpoints, a database of specific no-observed-effect levels (NOELs) was compiled by screening oral toxicity studies. The substances recorded in each specific database were selected on the basis of their demonstrated adverse effects. For the neurotoxicity and developmental neurotoxicity databases, it was intended to cover all classes of compounds reported to have either a demonstrated neurotoxic or developmentally neurotoxic effect, or at least, on a biochemical or pharmacological basis were considered to have a potential for displaying such effects. For the immunotoxicity endpoint, it was ensured that only immunotoxicants were included in the database by selecting most of the substances from the Luster et al. database, provided that they satisfied the criteria for immunotoxicity defined by Luster. For the developmental toxicity database, substances were selected from the Munro et al. database that contained the lowest NOELs retrieved from the literature for more than 600 compounds. After screening these, substances showing any effect which could point to developmental toxicity as broadly defined by the US were recorded in the database. Additionally, endocrine toxicity and allergenicity were addressed as two separate cases, using different approaches and methodology. The distributions of NOELs for the neurotoxicity, developmental neurotoxicity and developmental toxicity endpoints were compared with the distribution of NOELs for non-specific carcinogenic endpoints. As the immunotoxicity database was too limited to draw such a distribution of immune NOELs, the immunotoxicity endpoint was evaluated by comparing immune NOELs (or LOELs-lowest-observed-effect levels-when NOELs were not available) with non-immune NOELs (or LOELs), in order to compare the sensitivity of this endpoint with non-specific endpoints. A different methodology was adopted for the evaluation of the endocrine toxicity endpoint since data currently available do not permit the establishment of a clear causal link between endocrine active chemicals and adverse effects in humans. Therefore, this endpoint was analysed by estimating the human exposure to oestrogenic environmental chemicals and evaluating their potential impact on human health, based on their contribution to the overall exposure, and their estrogenic potency relative to endogenous hormones. The allergenicity endpoint was not analysed as such. It was addressed in a separate section because this issue is not relevant to the overall population but rather to subsets of susceptible individuals, and allergic risks are usually controlled by other means (i.e. labelling) than the Threshold of Toxicological Concern approach. (ABSTRACT TRUNCATED)

Effects of in utero and lactational exposure to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) on serum androgens and steroidogenic enzyme activities in the male rat reproductive tract

2,3,7,8-Tetrachlorodibenzo-p-dioxin (TCDD) has been shown to impair reproductive function of males in animal models, possibly due to a reduction in serum androgen levels. Thus, TCDD may alter the testosterone biosynthetic pathway in the testis or the conversion of testosterone to 5alpha-dihydrotestosterone (DHT) in androgen target tissues. Pregnant Sprague Dawley rats were gavaged with TCDD (0, 0.2 or 1.0 microg/kg) on day 15 of gestation only. TCDD caused a reduction in the body weight gain of the dams in both dose groups and a significant reduction in litter size in the higher dose group. Litters delivered normally and TCDD exposed male offspring grew at the same rate as controls. Males were sacrificed at 15, 30, 45, 60, 90 and 120 d of age. Steroidogenic enzyme activities were determined in testicular microsomes and androgen target tissue nuclear fractions. Serum androgens were measured by radioimmunoassay (RIA). At 30 d of age, rats exposed to 1.0 microg/kg TCDD exhibited lower 17-hydroxylase activity (P < 0.05) and lower caput-corpus epididymal weights (P < 0.05). At 45 d of age, the same treatment resulted in testicular 3beta-HSD, 17beta-HSD and 5alpha-reductase activities that were significantly greater (P < 0.05) but, conversely, serum androgens were one quarter the values evident in controls (P < 0.05). At the other ages, no differences were observed in serum androgens and, with the exception of lower 17beta-HSD activity at 90 d of age (P < 0.05), no other differences in testicular steroidogenic enzyme activities were found. 5Alpha-reductase activities in the androgen target tissues were also unchanged. Histological examination of testes showed that the spermatogenic profile was identical to controls at all ages.

Responsiveness of the adult male rat reproductive tract to 2,3,7,8-tetrachlorodibenzo-p-dioxin exposure: Ah receptor and ARNT expression, CYP1A1 induction, and Ah receptor down-regulation

Exposure to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) either in adulthood or during late fetal and early postnatal development causes a variety of adverse effects on the male rat reproductive system. It was therefore of interest to identify male rat reproductive organs and cell types within these organs that might be direct targets of TCDD exposure. Because TCDD toxicity could possibly be the result of alterations in gene transcription mediated by the TCDD/aryl hydrocarbon receptor (AhR)/AhR nuclear translocator (ARNT) complex, the presence of the AhR and ARNT in the various organs of the adult male reproductive tract was examined using Western blotting. Both proteins were detectable in all organs examined (testis, epididymis, vas deferens, ventral prostate, dorsolateral [combined dorsal and lateral] prostate, and seminal vesicle). Although technical difficulties precluded the immunohistochemical evaluation of AhR distribution in these organs, ARNT was localized in all organs in a variety of cell types, including germ cells, epithelial cells, fibroblasts, smooth muscle cells, and endothelial cells. Subcellular localization varied across organs and across cell types within these organs. In order to determine whether TCDD exposure could alter gene expression in these organs, animals were dosed with TCDD (25 micrograms/kg po) or vehicle and euthanized at 24 h, and cytochrome P4501A1 (CYP1A1) expression was evaluated. By Western blotting, only the ventral and dorsolateral prostates exhibited significant induction of CYP1A1. Immunohistochemistry confirmed this induction and localized CYP1A1 expression to epithelial cells of the ventral and lateral lobes of the prostate. Immunohistochemistry also revealed CYP1A1 induction in select epithelial cells in the epididymis and seminal vesicle, as well as endothelial cells in the vas deferens and seminal vesicle. No induction was observed in the testis. Finally, AhR and ARNT expression in TCDD-exposed and control animals was evaluated by Western blotting. Results revealed no effect of TCDD exposure on ARNT protein expression, while AhR expression was decreased to 5-51% of control in all organs examined. In summary, both AhR and ARNT were expressed in all organs of the adult male rat reproductive tract examined, and epithelial and/or endothelial cells within each of these organs (with the exception of the testis) were responsive to TCDD exposure in terms of CYP1A1 induction. In addition, all tissues exhibited marked reductions in AhR protein content after TCDD exposure that did not correlate with the magnitude of the CYP1A1 response.

Treatment of rats during pubertal development with 2,3,7,8-tetrachlorodibenzo-p-dioxin alters both signaling kinase activities and epidermal growth factor receptor binding in the testis and the motility and acrosomal reaction of sperm

Different doses of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) (0.1, 1, 5, and 10 micrograms/kg body wt) were administered i.p. to 21-day-old male Sprague-Dawley rats. Control animals received the same volume of the vehicle (acetone:corn oil, 1:19). Body weight and daily food intake were recorded during the 90-day time course of the study. Random samples of five rats were sacrificed at 34, 49, 62, and 90 days of age. Epidermal growth factor receptor (EGFR) in whole testis was measured, as were the activities of c-Src kinase, protein tyrosine kinase (PTK), mitogen-activated protein 2 kinase (MAP2K also termed as Erk2), protein kinase A (PKA), and protein kinase C (PKC). Testicular tissue from 90-day-old rats was evaluated for histopathology, and sperm numbers in whole testis were counted to estimate daily sperm production. The motility of sperm in the vas deferens and caudal segments of the epididymis of 90-day-old rats was measured by computer assisted sperm analysis (CASA) and the function of the sperm was tested by assessment of acrosome reactions. A dose of 10 micrograms/kg resulted in testicular atrophy and histopathologic examination revealed a decrease in the diameter of the seminiferous tubules. Sertoli cell nuclei were clearly seen, but the spermatogonial population was totally absent. Lower doses of TCDD did not affect testicular histology, but doses as low as 1 microgram/kg significantly decreased testicular sperm numbers and affected some sperm functions (motility parameters and acrosome reactions) in 90-day-old rats. Significant decreases in EGFR were found in 34-day-old rats and this effect on EGFR was sustained until the end of the experiment (90 days). Although TCDD significantly increased c-Src kinase activity in immature and mature rats, opposite effects of TCDD on activities of PTK, PKA, and PKC were found in 34-day-old rats vs 49-, 62-, and 90-day-old rats. When 10 micrograms TCDD/kg was administered to 21-day-old rat, 24-h after c-Src kinase inhibitor geldanamycin, there was no testicular atrophy and no change in the daily sperm production was found. These findings provide evidence for involvement of Src kinase signaling and EGFR in the mechanism by which TCDD disrupts testicular development and subsequently affects testis function.

Effects of chronic exposure to PCBs on cytochrome P450 systems and steroidogenesis in liver and testis of bulls (Bos taurus)

Effects of chronic exposure to PCBs on the microsomal cytochrome P450 (CYP) enzymes in liver and testis of bulls (Bos taurus) were determined by comparing the constitutive and PCB-induced alkoxyresorufin O-dealkylase and testosterone hydroxylase activities. Specific inductions of the prevailing hepatic ethoxyresorufin O-deethylation and 6 beta-hydroxylation of testosterone are suggestive of the induction of CYP1A1 and CYP3A-like enzymes by PCBs. A high level of PCB-inducible androstenedione formation was also found. The hepatic CYP2B activities (i.e. pentoxyresorufin O-depentylase and testosterone 16 beta-hydroxylase) and CYP2C11-like testosterone 2 alpha-hydroxylase were increased only weakly. The testicular microsomal CYP activities were non-specifically reduced by the PCB exposure, except for the androstenedione formation and 16 beta-hydroxylation of testosterone. The inhibition of the activity of mitochondrial CYP11A, as the rate-limiting enzyme of steroidogenesis measured with resorufin 3 beta-hydroxy-22,23-bisnor-5-cholenyl ether as the fluorogenic substrate, exceeded 50% in testes of the PCB-contaminated bulls. The latter activity as well as the hepatic testosterone 6 beta-hydroxylation and hepatic and testicular androstenedione formation may significantly contribute to the decrease in testosterone levels after the PCB intake.

Effects of Aroclor 1254 on the thyroid gland, immune function, and hepatic cytochrome P450 activity in mallards

Adult male mallards were exposed to 0, 4, 20, 100, 250, and 500 mg/kg Aroclor 1254 by gavage twice per week for 5 weeks. Immunotoxic effects, as measured by antibody titers to sheep erythrocytes, natural killer cell activity and lymphocyte mitogenesis to phytohemagglutinin, were not detected as a consequence of polychlorinated biphenyl (PCB) exposure. Hepatic cytochrome P450 activities were measured as microsomal dealkylations of ethoxyresorufin (EROD) and pentoxyresorufin (PROD). Significant elevations in EROD and PROD were noted at 20 mg/kg and peaked in birds treated with 100 mg/kg. Total P450 was induced beginning at 100 mg/kg and peaked at 250 mg/kg. Relative liver weights were dose-dependently increased following treatment with 100 mg/kg or more. Thyroid weights were significantly increased in PCB-treated birds treated with 100 mg/kg or greater, but no significant histological abnormalities were observed, except at the highest dose. Plasma total triiodothyronine (T3) was decreased in a dose-dependent manner, with a significant lowest-observed-adverse-effect level (LOAEL) of 20 mg/kg. T3 was decreased following 7 days treatment with 100 mg/kg. The no-observed-adverse-effect level (NOAEL) was 4 mg/kg for decreased T3. Plasma glucose levels were decreased on days 28 and 35 in mallards treated with 500 mg/kg, while other clinical plasma biochemistry parameters were unaltered by PCB treatment. Plasma corticosterone levels were unchanged by PCB treatment. These results indicate that thyroid hormone levels and P450 activity in mallards are sensitive to subchronic PCB exposure in the absence of gross toxic effects and immunotoxicity.

The effect of the aromatase inhibitor fadrozole and two polynuclear aromatic hydrocarbons on sex steroid secretion by ovarian follicles of coho salmon

A variety of endogenous and exogenous factors can influence sex steroid production by salmon ovarian follicles and ultimately impact reproductive development. We examined the effect of an aromatase inhibitor, fadrozole, and common environmental contaminants (PAHs) on sex steroid secretion by ovarian follicles. Ovarian follicles of coho salmon were incubated in vitro with various concentrations of testosterone (0.10-0.40 microM) and fadrozole (10 and 100 microM), or with varying doses (between 0.05 and 5.0 microM) of the PAHs beta-naphthoflavone (BNF) and 20-methylcholanthrene (20-MC). 17 beta-Estradiol secretion was significantly reduced when follicles were incubated in the presence of fadrozole, BNF, or 20-MC. In contrast, 17 beta-estradiol production by ovarian follicles increased in a dose-dependent manner when incubated with increasing doses of the aromatizable androgen testosterone. Although increasing doses of PAHs significantly reduced follicular 17 beta-estradiol production no effect on testosterone secretion was observed. Hence, both fadrozole and PAHs can significantly reduce 17 beta-estradiol secretion by salmon ovarian follicles and may affect female sexual development.

Mechanism by which 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) reduces circulating melatonin levels in the rat

We have previously shown that the prototype for halogenated aromatic hydrocarbons, 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), diminishes serum melatonin concentration at the same dose in both the most TCDD-susceptible (Long-Evans, Turku AB; L-E) and the most TCDD-resistant (Han/Wistar, Kuopio; H/W) rat strain. The change developed within 24 h and persisted for at least 28 days after TCDD exposure; was independent of the time of day and was not associated with any morphological damage to the pineal gland. In the present study, we investigated the mechanism of this endocrine effect. Despite a 40-50% decrease in circulating melatonin levels, the pineal content of melatonin, serotonin and 5-hydroxyindole acetic acid remained unaltered and the rate-limiting enzyme of pineal melatonin biosynthesis, N-acetyltransferase, displayed only a relatively minor suppression in activity (30%) in TCDD-treated L-E rats. Likewise, TSDD did not influence the ability of pineal glands from L-E rats to synthesize and secrete melatonin in ex vivo or in vitro experiments. TCDD accelerated the disappearance of exogenous melatonin from the serum in both rat strains. This enhancement probably did not originate in the liver, because liver perfusion studies revealed that even control rat livers were capable of total melatonin clearance in spite of the fact that the melatonin concentration far exceeded physiological levels. Urine excretion of the normal main metabolite of melatonin, 6-hydroxymelatoninsulfate, was reduced by TCDD treatment in both strains. This was accompanied by an altered HPLC pattern of metabolites, especially in H/W rats. We conclude that TCDD decreases serum melatonin levels in rats by enhancing the peripheral, evidently extrahepatic, metabolism of the hormone.

Human chorionic gonadotropin protects Leydig cell function against 2,3,7,8-tetrachlorodibenzo-p-dioxin in adult rats: role of Leydig cell cytoplasmic volume

2,3,7,8-Tetrachlorodibenzo-p-dioxin (TCDD) alters testicular steroidogenesis and reduces Leydig cell volume and number; however, human chorionic gonadotropin (hCG) stimulates testosterone production, increases the number and volume of Leydig cells and prevents TCDD's inhibition of testosterone production. The objective of this study was to determine if hCG protects Leydig cell function by maintaining sufficient Leydig cell cytoplasmic volume in TCDD-treated rats. Adult, male Sprague Dawley rats were divided into six treatment groups. Half of the animals received TCDD in corn oil (50 micrograms/kg body wt) and half received corn oil alone on Day 7 only. Additionally the rats received daily treatment of saline for 14 days, saline for 7 days and then hCG for 7 days, or hCG for 14 days. Rats were sacrificed on Day 14 and tissues collected. The decapsulated left testes were incubated in Eagles MEM for 2 h to determine basal production of testosterone and for 2 additional hours after the addition of hCG (100 IU) to the culture media. The right testis was evaluated by stereology to determine the volume of Leydig cells. Body weight was reduced (P < 0.01) in each TCDD-treated group; whereas, testicular weight was not affected by TCDD or hCG treatment. hCG prevented the TCDD-induced reduction in prostate and seminal vesicles weights. TCDD reduced the total volume of Leydig cell cytoplasm in saline-treated rats, but hCG eliminated the TCDD-induced reduction in Leydig cell cytoplasmic volume. hCG prevented the TCDD-induced reduction in Leydig cell function for both the 7- and 14-day treatments. Variation in the total volume of Leydig cell cytoplasm induced by the various treatment combinations was positively correlated with stimulated testosterone production in vitro (r = 0.486; P < 0.01) and the weight of the androgen sensitive organs (seminal vesicles, r = 0.562, P < 0.01; prostate, r = 0.380, P < 0.05). These data support the hypothesis that hCG prevents the TCDD-reduced Leydig cell function by maintaining sufficient Leydig cell cytoplasm and organelle content.

Modulation of gene expression and endocrine response pathways by 2,3,7,8-tetrachlorodibenzo-p-dioxin and related compounds

The aryl hydrocarbon (Ah) receptor binds several different structural classes of chemicals, including halogenated aromatics, typified by 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), polynuclear aromatic and heteropolynuclear aromatic hydrocarbons. TCDD induces expression of several genes including CYP1A1, and molecular biology studies show that the Ah receptor acts as a nuclear ligand-induced transcription factor that interacts with xenobiotic or dioxin responsive elements located in 5'-flanking regions of responsive genes. TCDD also elicits diverse toxic effects, modulates endocrine pathways and inhibits a broad spectrum of estrogen (17 beta-estradiol)-induced responses in rodents and human breast cancer cell lines. Molecular biology studies show that TCDD inhibited 17 beta-estradiol-induced cathepsin D gene expression by targeted interaction of the nuclear Ah receptor with imperfect dioxin responsive elements strategically located within the estrogen receptor-Sp1 enhancer sequence of this gene.

2,3,7,8-Tetrachlorodibenzo-p-dioxin reduces the number, size, and organelle content of Leydig cells in adult rat testes

Exposure to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) alters testicular steroidogenesis and reduces total Leydig cell volume in the testis. However, its effect on Leydig cell number, size, and organelle content had not been determined in adult rats. Adult male rats received a single intraperitoneal injection of TCDD at a dose of 0, 12.5, 25.0, or 50.0 micrograms/kg body weight. Testicular tissues were obtained from rats 4 weeks after treatment. Testes were vascularly perfused with glutaraldehyde, embedded in Epon 812, sectioned at 0.5 micron, stained with toluidine blue, and evaluated by stereology for number and size of Leydig cells. Specimens from control and high dose groups were prepared for electron microscopy to quantify Leydig cell organelle content. TCDD treatment reduced (P < 0.01) body weight in a dose-dependent fashion. Testicular weight was not significantly reduced by TCDD treatment. The volume of Leydig cell cytoplasm per testis was reduced (P < 0.01) four weeks after treatment. Reduction in total Leydig cell volume resulted from a reduced (P < 0.05) number of Leydig cells and a reduced (P < 0.01) size of individual Leydig cells. However, the volume density (percentage) of Leydig cells occupied by specific organelles was not influenced by TCDD treatment. As a result of reduced total Leydig cell volume with no change in volume density of organelles in Leydig cells, the volumes per testis of smooth endoplasmic reticulum and mitochondria were reduced (P < 0.01) by TCDD treatment. In conclusion, the TCDD-induced reduction in Leydig cell volume per testis is explained by reduced number and size of individual Leydig cells and resulted in a significant reduction in total volume of both Leydig cell smooth endoplasmic reticulum and mitochondria per testis. Reduction in content of organelles that are responsible for various key steps in steroidogenesis, could explain TCDD-reduced production of testosterone in rats.

Developmental and reproductive toxicity of dioxins and related compounds: cross-species comparisons

Developmental toxicity to TCDD-like congeners in fish, birds, and mammals, and reproductive toxicity in mammals are reviewed. In fish and bird species, the developmental lesions observed are species dependent, but any given species responds similarly to different TCDD-like congeners. Developmental toxicity in fish resembles "blue sac disease," whereas structural malformations can occur in at least one bird species. In mammals, developmental toxicity includes decreased growth, structural malformations, functional alterations, and prenatal mortality. At relatively low exposure levels, structural malformations are not common in mammalian species. In contrast, functional alterations are the most sensitive signs of developmental toxicity. These include effects on the male reproductive system and male reproductive behavior in rats, and neurobehavioral effects in monkeys. Human infants exposed during the Yusho and Yu-Cheng episodes, and monkeys and mice exposed perinatally to TCDD developed an ectodermal dysplasia syndrome that includes toxicity to the skin and teeth. Toxicity to the central nervous system in monkey and human infants is a potential part of the ectodermal dysplasia syndrome. Decreases in spermatogenesis and the ability to conceive and carry a pregnancy to term are the most sensitive signs of reproductive toxicity in male and female mammals, respectively.

Sensitivity of Sertoli and Leydig cells to xenobiotics in in vitro models

Different chemicals are known to cause testicular damage in the human male and experimental animals. However, the ability to assess the potential and mechanism of action leading to chemically-induced damage in men has been hampered by a lack of good predictive models. Although many of these chemicals were found to impair reproductive capacity in various laboratory animals, only some have caused reproductive damage in men. Mammalian spermatogenesis takes places within the avascular seminiferous tubules of the testis. Specialized tight junctions, which form between adjacent Sertoli cells at the time of puberty, divide the tubular space into the basal and adluminal compartments, and create a "blood-testis" barrier that restricts passage of substances and ions from the circulation. Thus, the completion of meiosis and post-meiotic germ cell differentiation, which take place in the adluminal compartment, are isolated from circulating substances unable to cross the blood-testis barrier. It seems feasible, therefore, that damage to the germ cells induced by testicular toxicants may be mediated through other cells in the testis such as the Sertoli, peritubular, or Leydig cells. A recently developed two-compartment system for culture of testicular cells can simulate, to some degree, the normal physiologic conditions. In principle, Sertoli cells isolated from mammalian testes are cultured on a permeable support (that is millipore filter) between two fluid compartments. They form a highly polarized epithelial layer with characteristic tight junctions that restrict the passage of substances between the two compartments, in analogy to the blood-testis barrier. We believe this system provides an excellent in vitro model for determining the ability of chemicals to: a) alter the permeability of the blood-testis barrier, b) impair the secretory function of Sertoli cells, or c) affect their viability, all of which could indirectly affect the germ cells. We have utilized this system for examining the effects of cadmium chloride (CdCl2) and other toxic substances known to affect the testis. The Leydig cell toxicity was investigated in testicular perfusion system or cultures of isolated Leydig cells.

Exposure to bleached kraft pulp mill effluent disrupts the pituitary-gonadal axis of white sucker at multiple sites

Our recent studies have demonstrated reproductive problems in white sucker (Catostomus commersoni) exposed to bleached kraft pulp mill effluent (BKME) at Jackfish Bay on Lake Superior. These fish exhibit delayed sexual maturity, reduced gonadal size, reduced secondary sexual characteristics, and circulating steroid levels depressed relative to those of reference populations. The present studies were designed to evaluate sites in the pituitary-gonadal axis of prespawning white sucker affected by BKME exposure. At the time of entry to the spawning stream, plasma levels of immunoreactive gonadotropin (GtH)-II (LH-type GtH) in male and female white sucker were 30- and 50-fold lower, respectively, than the levels in fish from a reference site. A single intraperitoneal injection of D-Arg6, Pro9N-Et sGnRH (sGnRH-A, 0.1 mg/kg) increased plasma GtH levels in male and female fish at both sites, although the magnitude of the response was greatly reduced in BKME-exposed fish. Fish at the BKME site did not ovulate in response to sGnRH-A, while 10 of 10 fish from the reference site ovulated within 6 hr. Plasma 17 alpha,20 beta-dihydroxy-4-pregnen-3-one (17,20 beta-P) levels were depressed in BKME-exposed fish and unlike fish at the reference site, failed to increase in response to sGnRH-A. Testosterone levels in both sexes and 11-ketostestosterone levels in males were elevated in fish from the reference site but were not further increased by GnRH treatment. In contrast, BKME-exposed fish exhibit a transitory increase in testosterone levels in response to the GnRH analog. In vitro incubations of ovarian follicles obtained from fish at the BKME site revealed depressed basal secretion of testosterone and 17,20 beta-P and reduced responsiveness to the GtH analog human chorionic gonadotropin and to forskolin, a direct activator of adenylate cyclase. By comparison, ovarian follicles from fish collected at BKME and reference sites produced similar levels of prostaglandin E basally and in response to a phorbol ester and calcium ionophore A23187, suggesting that BKME effects on ovarian function are selective and do not reflect a general impairment of ovarian function. BKME-exposed fish had plasma levels of testosterone glucuronide proportionately lower than those of reference fish, suggesting that there are site differences in the peripheral metabolism of steroids. These studies demonstrate that BKME exposure affects reproduction by acting at multiple sites in the pituitary-gonadal axis.

In utero and lactational exposure of male rats to 2,3,7,8-tetrachlorodibenzo-p-dioxin. 3. Effects on spermatogenesis and reproductive capability

When administered in overtly toxic doses to postweanling male rats, 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) produces adverse effects on the reproductive system including a decrease in spermatogenesis. Because the male reproductive system may be particularly susceptible to toxic insult during the perinatal period, the effects of in utero and lactational TCDD exposure on its development were examined. Male rats born to dams given TCDD (0.064, 0.16, 0.40, or 1.0 micrograms/kg, po) or vehicle on Day 15 of gestation were evaluated at various stages of development; effects on spermatogenesis and male reproductive capability are reported herein. Testis, epididymis, and cauda epididymis weights were decreased in a dose-related fashion at 32, 49, 63, and 120 days of age, that is, when males were at the juvenile, pubertal, postpubertal, and mature stages of sexual development, respectively. When measured on Days 49, 63, and 120, daily sperm production by the testis was reduced at the highest maternal TCDD dose to 57-74% of the control rate. Cauda epididymal sperm reserves in 63- and 120-day-old males were decreased to as low as 25 and 44%, respectively, of control values, although the motility and morphology of these sperm appeared to be unaffected. The magnitude of the effects described above tended to lessen with time; nevertheless, the decreases in epididymis and cauda epididymis weights, daily sperm production, and cauda epididymal sperm number were statistically significant at the lowest maternal dose tested (0.064 micrograms TCDD/kg) on Day 120 and at most earlier times. To determine if in utero and lactational TCDD exposure also affects male reproductive capability, rats were mated at approximately 70 and 120 days of age with control females. Little if any effect on fertility was seen, and the survival and growth of offspring was unaffected. These results are not inconsistent with the pronounced reductions in daily sperm production and cauda epididymal sperm reserves caused by perinatal TCDD exposure since rats produce and ejaculate far more sperm than are required for normal fertility. The TCDD-induced reduction in spermatogenesis cannot be accounted for by concurrent effects on plasma follicle-stimulating hormone or androgen concentrations or by undernutrition. To investigate the nature of the spermatogenic lesion, leptotene spermatocyte to Sertoli cell ratios were determined.(ABSTRACT TRUNCATED AT 400 WORDS)

Induction of Leydig cell adenomas by ammonium perfluorooctanoate: a possible endocrine-related mechanism

Ammonium perfluorooctanoate (C8) produced an increased incidence of Leydig cell adenomas in Crl:CD BR (CD) rats fed 300 ppm for 2 years. A hormonal (nongenotoxic) mechanism was examined since C8 was negative in short-term tests for genotoxicity. Adult male CD rats were gavaged with either 0, 1, 10, 25, or 50 mg/kg C8 for 14 days. In addition, a control group was pair-fed to the 50 mg/kg C8 group. A dose-dependent decrease in body and relative accessory sex organ (ASO) weights was seen, with the relative ASO weights of the 50 mg/kg group significantly less than those of the pair-fed control. Serum estradiol levels were elevated in the 10, 25, and 50 mg/kg C8-treated animals. Estradiol levels in the 50 mg/kg C8 group were 2.7-fold greater than those in the pair-fed control. The increase in serum estradiol levels occurred at the same dose levels as the increase in hepatic beta-oxidation activity. A statistically significant downward trend with dose was seen in serum testosterone levels when compared with the ad libitum control. However, when the 50 mg/kg C8-treated rats were compared with their pair-fed control, no significant differences were seen. Challenge experiments, which can identify the presence and location of a lesion in an endocrine axis, were undertaken to clarify the significance of this downward trend in serum testosterone following C8 exposure. In the challenge experiments, adult CD rats were gavaged with either 0 or 50 mg/kg C8 for 14 days. One hour before termination, rats received either a human chorionic gonadotropin (hCG), gonadotropin-releasing hormone (GnRH), or naloxone challenge. Following hCG challenge, serum testosterone levels in the 50 mg/kg C8 were significantly decreased (50%) from those in the ad libitum controls. Similar decreases, although not significant, were seen in serum testosterone following GnRH and naloxone challenge. The challenge experiments suggest that the decrease in serum testosterone following C8 exposure is due to a lesion at the level of the testis. In addition, progesterone, 17 alpha-hydroxyprogesterone, and androstenedione were examined in the 50 mg/kg C8-treated males following hCG challenge. A 60% decrease was observed in androstenedione levels in the C8-treated animals from those in the ad libitum controls; no other differences were seen. These data suggest that the decrease in serum testosterone following hCG challenge may be due to a decrease in the conversion of 17 alpha-hydroxyprogesterone to androstenedione. The observed effects described above can be attributed to the elevated serum estradiol levels.(ABSTRACT TRUNCATED AT 400 WORDS)