Search

The objective of toxicological study of a target organ, such as the testis, is to elucidate the qualitative and quantitative toxic effects of a chemical on that organ. The ultimate objective is to assess the toxic effects of a chemical in laboratory animals and extrapolate the pertinent experimental data to man. To accomplish these objectives, one must consider the main factors which may influence and modulate the toxic effects of chemicals in the organ. In the male gonads, such modifying factors are the pharmacokinetic parameters governing the absorption, distribution, activation and detoxification of indirect carcinogens, covalent bindings to macromolecules, and DNA damage as well as DNA repair of damaged germ cells. All of these factors have been presently studied in our laboratory and are discussed in this paper with the exception of covalent bindings to macromolecules.The pharmacokinetic studies demonstrated that the functional blood-testis barrier (BTB) closely resembles the blood-brain barrier in transport characteristics: the permeability of nonelectrolytes and the acidic drugs with pK(a) values depend upon their molecular size and their partition coefficients, respectively. Thus, the functional BTB, restricts the permeability of many foreign compounds to male germ cells. Studies of mixed function oxidases and cytochrome P-450 system in male gonads demonstrated that the presence of AHH, EH, and GSH-ST implicate activation and detoxification of polycyclic hydrocarbons. Thus, active electrophiles may exert significant toxic effects locally within both interstitial and germ cell compartments. The presence of an efficient DNA repair system in premeiotic spermatogenic cells (and not in spermiogenic cells) can further modify both toxic and mutagenic events in the subsequent differentiation of germ cells to mature spermatozoa.

Exposure of mice to 1000 ppm of vinyl chloride (VC), 6 hr/day, 5 days/week, caused some acute deaths with toxic hepatitis and marked tubular necrosis of the renal cortex. Starting the sixth month, mice exposed to 1000, 250, or 50 ppm of VC became lethargic, lost weight quickly, and died. Only a few mice exposed to 50 ppm survived for 12 months. Pulmonary macrophage count was elevated in some mice. There was a high incidence of bronchiolo-alveolar adenoma, mammary gland tumors including ductular adenocarcinoma, squamous and anaplastic cell carcinomas with metastasis to the lung, and hemangiosarcoma in the liver, and, to a lesser extent, in some other organs. The incidence of these tumors quickly increased, and the severity was in direct proportion to the levels of VC and the length of exposure. Malignant lymphoma involving various organs was observed in a few mice. Rats were more resistant to the toxic effects of VC. Exposure to 1000 ppm slightly depressed the body weight of the females. Exposures of 250 or 1000 ppm caused a number of deaths and hemangiosarcoma in the liver starting the ninth month. Most rats with hepatic hemangiosarcoma also developed hemangiosarcoma in the lung. Hemangiosarcoma occasionally occurred in other tissues of one or two rats exposed to 50 ppm or higher level of VC. Exposure of mice to 55 ppm of vinylidene chloride (VDC) also caused a few acute deaths and a few hepatic hemangiosarcomas. Inflammatory, degenerative, and mitotic changes occurred in the liver. No mouse exposed to VDC developed any mammary gland tumors. Several mice had bronchioloalveolar adenoma. Exposure of rats to 55 ppm of VDC slightly depressed the body weight. Hemangiosarcoma occurred in the mesenteric lymph node or subcutaneous tissue in two rats.

Some of the problems in extrapolating laboratory animal toxicity data to man are considered. The quantitative predictiveness of preclinical studies of anticancer drugs using dogs and monkeys for man has also been examined. The relationship between the maximum tolerated dose (MTD) in the dog, monkey, and the more sensitive of the two species and clinical observations are discussed. The effectiveness of using doses expressed on the basis of body weight (mg/kg) and body surface area (mg/m2) are compared. A method is introduced to assess the "statistical risk" associated with the extrapolation of the initial clinical (phase I) dose from experimental animal data. The best clinical prediction is obtained when one uses the experimental MTD expressed in mg/kg for the more sensitive of the large animal species (dogs or monkeys). The clinical introduction of a new anticancer agent at a dose 1/10 the MTD in the more sensitive species carries a statistical risk of about 3%; that is, the initial doses of about 3 of every 100 new drugs introduced into the clinic will produce some toxic effects in man. These same data have been extended theoretically to the total population and toxic chemicals in general. Reliable extrapolation from laboratory test models to man requires a much more complete understanding of structure--activity relationships, pharmacokinetic factors, and mechanisms of toxicity.

Exposure to drinking water containing as much as 500 ppm aluminum chloride for periods of 30, 60, and 90 days had no apparent effect on male reproductive processes. In an attempt to correlate enzyme activity with particular spermatogenic cell types, postnatal development of testicular enzymes was studied. Eight enzymes were selected: hyaluronidase (H), lactate dehydrogenase isoenzyme-X (LDH-X), dehydrogenases of sorbitol (SDH), alpha-glycerophosphate (GPDH), glucose-6-phosphate (G6PDH), malate (MDH), glyceraldehyde-3-phosphate (G3PDH), and isocitrate (ICDH). Enzyme specific activities in testicular homogenates were determined. Two types of enzyme developmental patterns were observed. One was represented by H, LDH-X, SDH, and GPDH; and the other by G6PDH, MDH, G3PDH, and ICDH. The former was characterized by a change in enzyme activities from low in newborn to high in adult while in the latter this pattern was reversed. The two complementary enzyme systems crossed each other at puberty. Prior to puberty, only spermatogonial cells are present; sperm differentiation initiated at puberty adds spermatocytes and spermatids to the testicular cell population. Male rats were exposed to borax in their diet for periods of 30 and 60 days. Concentrations of boron were 0, 500, 1000, and 2000 ppm. At the end of each experimental period, the specific activities of the selected enzymes were determined in the testis and prostate. Correlations of enzyme activity with testicular histology and androgen activities of the male accessory organs were sought. In addition, plasma FSH, LH, and testosterone levels were measured to assess pituitary-testicular interaction. Plasma and testicular boron concentrations were determined and a minimum boron concentration which induced germinal aplasia and male infertility was estimated. In both 30 and 60 day feeding studies, male rats receiving 500 ppm failed to demonstrate any significant adverse effects. In contrast, male rats receiving 100 and 2000 ppm boron displayed a significant loss of germinal elements, although most of the Leydig and Sertoli cells appeared normal. Testicular atrophy was associated with a decrease in seminiferous tubular diameter and a marked reduction of spermatocytes and spermatogenic cells. These morphologic alterations were associated with a concomitant reduction of H, SDH, and LDH-X specific activities. In contrast, the specific activities of G3PDH and MDH were significantly elevated above control. The increase in these enzyme activities can be attributed to the relative enrichment of spermatogonial cells during the loss of spermatocytes and spermiogenic cells. Boron-induced male germinal aplasia was also associated with significantly elevated plasma FSH while plasma LH and testosterone levels were not significantly altered. Plasma testosterone levels were unaltered. Male fertility studies demonstrated that at the 500 ppm boron level, fertility was unaffected. However, at 1000 and 2000 ppm boron, male fertility was significantly reduced. Most effects were reversible within 5 weeks. However, the male group receiving 2000 ppm boron for 60 days remained sterile. There was no dose-related decrease in litter size or fetal death in utero. Therefore, the boron-induced infertility was apparently not due to a dominant lethal effect but rather to germinal aplasia. Boron appears toxic to spermatogenic cells at testicular concentrations of 6-8 ppm.

Results of a U.S.S.R.--U.S. cooperative laboratory effort to improve and validate experimental techniques used to assess subtle reproductive effects in male laboratory animals are reported. The present studies attempted to evaluate the reproductive toxicity of cadmium as cadmium chloride and boron as borax (Na2B4O7) and to investigate the mechanism of toxicity in the rat following acute and subchronic oral exposure. In vitro cell separation techniques, in vivo serial mating tests, and plasma assays for hormones were utilized. Effects on the seminal vesicle and prostate were evaluated with chemical and enzyme assays. Clinical chemistry was monitored routinely. Acute oral doses, expressed as boron were 45, 150, and 450 mg/kg while doses for cadmium equivalent were 6.25, 12.5, and 25 mg/kg. Rats were also allowed free access to drinking water containing either boron (0.3, 1.0, and 6.0 mg/l.) or cadmium (0.001, and 0.l mg/l.) for 90 days. Randomly selected animals were studied following 30, 60, and 90 days of treatment. These initial studies, utilizing a variety of methods to assess the reproductive toxicity of environmental substances in male animals, suggest that cadmium and boron at the concentrations and dose regimens tested are without significant reproductive toxicity.