The comparative effects of 1,2-dibromo-3-chloropropane (DBCP) and its metabolites, 3-chloro-1,2-propaneoxide (epichlorohydrin), 3-chloro-1,2-propanediol (alphachlorohydrin), and oxalic acid, on the urogenital system of male rats

Chloropropanols and Their Esters in Food: An Updated Review

Chloropropanols, their fatty acid esters, and glycidol and its fatty acid esters (GEs) are process contaminants in foods that pose potential health risks. These contaminants typically arise during the deodorization process of vegetable oils, particularly in high concentrations within oils like palm oil and products derived from them, such as margarine, baked goods, pastries, and infant formula. Chloropropanol esters and GE can hydrolyze under the influence of lipases, forming chloropropanols. Elevated temperatures during food production can lead to the release of free 3-chloro-1,2-propanediol (3-MCPD) or free 2-chloro-1,3-propanediol (2-MCPD) in products containing both fat and salt. The exposure to these contaminants, especially for infants and young children, raises concerns about potential health hazards. While extensive research has focused on 3-MCPD, 2-MCPD, and GE, knowledge regarding other chloropropanols such as 1,3-dichloro-2-propanol (1,3-DCP), 2,3-dichloro-1-propanol (2,3-DCP), and their fatty acid esters remains limited. This review aims to provide a comprehensive overview encompassing formation mechanisms, analysis methods, toxicological implications, occurrence patterns, exposure levels, mitigation strategies, and legislative considerations concerning these contaminants.

Carcinogenicity of Monochloro-1,2-Propanediol (α-Chlorohydrin, 3-MCPD)

3-Monochloro-1,2-propanediol (3-MCPD) is a by-product found in trace amounts, generally less than 1 mg/kg (<1 ppm), in hydrolyzed vegetable protein produced through acid hydrolysis. In a chronic study with F344 rats, high doses of 3-MCPD produced benign renal tumors in both sexes and Leydig-cell and mammary tumors in males. 3-MCPD is genotoxic in vitro, but there is no evidence of genotoxicity in vivo. There is some question about the mechanism responsible for the carcinogenicity of 3-MCPD in certain species. Here we present a critical review of the toxicological, metabolic, and mechanistic data on 3-MCPD. On the basis of this review, the tumors reported in F344 rats are concluded to have developed as a result of nongenotoxic mechanisms and are considered not to be relevant to humans exposed to trace amounts of 3-MCPD. This conclusion was based on the lack of carcinogenicity of 3-MCPD in mice or Sprague-Dawley rats; the benign nature of the tumors involved; the dependence of the Leydig-cell and mammary tumors on species-and strain-dependent mechanisms involving chronic changes in hormone balance; the association of the renal tumors with chronic nephropathy and nephrotoxicity; and differences between bacterial and mammalian systems in the metabolism of 3-MCPD that likely account for its genotoxic activity in certain in vitro test systems. At trace levels in foods, 3 MCPD is considered not to pose a carcinogenic risk to humans.

Cytotoxicity, genotoxicity, and mutagenicity of 1-chloro-2-hydroxy-3-butene and 1-chloro-3-buten-2-one, two alternative metabolites of 1,3-butadiene

The cytotoxicity, genotoxicity, and mutagenicity of 1-chloro-2-hydroxy-3-butene (CHB), a known in vitro metabolite of the human carcinogen 1,3-butadiene, have not previously been investigated. Because CHB can be bioactivated by alcohol dehydrogenases to yield 1-chloro-3-buten-2-one (CBO), a bifunctional alkylating agent that caused globin-chain cross-links in erythrocytes, in the present study we investigated the cytotoxic and genotoxic potential of CHB and CBO in human normal hepatocyte L02 cells using the MTT assay, the relative cloning efficiency assay and the comet assay. We also investigated the mutagenic potential of these compounds with the Ames test using Salmonella strains TA1535 and TA1537. The results provide clear evidence for CHB and CBO being both cytotoxic and genotoxic with CBO being approximately 100-fold more potent than CHB. Interestingly, CHB generated both single-strand breaks and alkali-labile sites on DNA, whereas CBO produced only alkali-labile sites. CHB did not directly result in DNA breaks, whereas CBO was capable of directly generating breaks on DNA. Interestingly, both compounds did not induce DNA cross-links as examined by the comet assay. The Ames test results showed that CHB induced point mutation but not frameshift mutation, whereas the toxic effects of CBO made it difficult to reliably assess the mutagenic potential of CBO in the two strains. Collectively, the results suggest that CHB and CBO may play a role in the mutagenicity and carcinogenicity of 1,3-butadiene.

Alcohol dehydrogenase- and rat liver cytosol-dependent bioactivation of 1-chloro-2-hydroxy-3-butene to 1-chloro-3-buten-2-one, a bifunctional alkylating agent

1,3-Butadiene (BD) is an air pollutant whose toxicity and carcinogenicity have been considered primarily mediated by its reactive metabolites, 3,4-epoxy-1-butene and 1,2,3,4-diepoxybutane, formed in liver and extrahepatic tissues by cytochromes P450s. A possible alternative metabolic pathway in bone marrow and immune cells is the conversion of BD to the chlorinated allylic alcohol 1-chloro-2-hydroxy-3-butene (CHB) by myeloperoxidase in the presence of hydrogen peroxide and chloride ion. In the present study, we investigated the in vitro bioactivation of CHB by alcohol dehydrogenases (ADH) under in vitro physiological conditions (pH 7.4, 37 °C). The results provide clear evidence for CHB being converted to 1-chloro-3-buten-2-one (CBO) by purified horse liver ADH and rat liver cytosol. CBO readily reacted with glutathione (GSH) under assay conditions to form three products: two CBO-mono-GSH conjugates [1-chloro-4-(S-glutathionyl)butan-2-one (3) and 1-(S-glutathionyl)-3-buten-2-one (4)] and one CBO-di-GSH conjugate [1,4-bis(S-glutathionyl)butan-2-one (5)]. CHB bioactivation and the ratios of the three GSH conjugates formed were dependent upon incubation time, GSH and CHB concentrations, and the presence of ADH or rat liver cytosol. The ADH enzymatic reaction followed Michaelis-Menten kinetics with a K(m) at 3.5 mM and a k(cat) at 0.033 s(-1). After CBO was incubated with freshly isolated mouse erythrocytes, globin dimers were detected using SDS-PAGE and silver staining, providing evidence that CBO can act as a protein cross-linking agent. Collectively, the results provide clear evidence for CHB bioactivation by ADH and rat liver cytosol to yield CBO. The bifunctional alkylating ability of CBO suggests that it may play a role in BD toxicity and/or carcinogenicity.

Spermatotoxic effects of α-chlorohydrin in rats

This study was conducted to investigate the potential effects of α-chlorohydrin (ACH) on epididymal function and antioxidant system in male rats. The test chemical was administered to male rats by gavage at doses of 0, 3, 10, and 30 mg/kg/day for 7 days. Twenty-four male rats were randomly assigned to four experimental groups, with six rats in each group. Spermatotoxicity was assessed by measurement of reproductive organ weight, testicular sperm head count, epididymal sperm motility and morphology, histopathologic examination, and oxidative damage analysis in rats. At 30 mg/kg/day, an increase in the incidence of clinical signs, epididymis weight, and gross necropsy findings of the epididymis, a decrease in the sperm motility, and an increased incidence of histopathological changes of the epididymis were observed in a dose-dependent manner. At 10 mg/kg/day, an increased incidence of clinical signs and histopathological changes and decreased sperm motility were observed. In the oxidative damage analysis, an increase in the malondialdehyde concentration and a decrease in the glutathione content and glutathione peroxidase and catalase activities in the epididymal tissue were detected at ≥3 mg/kg/day. The results show that graded doses of ACH elicit depletion of the antioxidant defense system and that the spermatotoxicity of ACH may be due to the induction of oxidative stress.

Lack of effect on rat testicular organogenesis after in utero exposure to 3-monochloropropane-1,2-diol (3-MCPD)

3-Monochloropropane-1,2-diol (3-MCPD) is a food-born contaminant known to display toxic effects on male reproduction, producing infertility in rats and humans. Using the rat as a model, we investigated whether or not testicular organogenesis, which, in the rat species, occurs during the second half of gestation, was at particular risk regarding 3-MCPD toxicity. Pregnant rats were given daily doses of 5, 10 or 25 mg/kg BW of 3-MCPD from days 11.5-18.5 postcoitum (dpc). On 19.5 dpc, testes were removed from fetuses for histological examination and testosterone analysis. Eight genes were selected among the differentiation markers of testicular cell lineages, and their expression was studied by RT-PCR. The levels of 3-MCPD and its main metabolite, beta-chlorolactic acid, were assayed in fetal tissues and dam plasma. Our results show a statistically significant decrease in the mean body weight gain of pregnant rats treated with 10 and 25 mg/kg BW of 3-MCPD. Fetal testes exposed to 3-MCPD exhibited normal histology and produced testosterone at levels that were similar to controls. In addition, 3-MCPD did not alter gene expression in the fetal testes. This lack of effect occurred under conditions where 3-MCPD and beta-chlorolactic acid were found to readily cross the placental barrier and diffuse throughout the fetal tissues. Our findings indicate that 3-MCPD has minimal effect on rat testicular organogenesis.

Pathogenetic transition in the morphology of abnormal sperm in the testes and the caput, corpus, and cauda epididymides of male rats after treatment with 4,6-dinitro-o-cresol

In order to elucidate the pathogenesis of tailless sperm, 4,6-dinitro-o-cresol (DNOC) was administered to Jcl:SD male rats at daily oral doses of 0, 10 or 15mg/kg for 5 days. Sperm were collected from the caput, corpus, and cauda epididymides on days 1, 7 and 14 after the last dosing (D1, D7 and D14, respectively), counted and examined morphologically by phase-contrast and scanning electron microscopy. The incidence of abnormal sperm was significantly increased in the DNOC 15mg/kg group. On D1, peeled sperm (loss of mitochondrial sheath at the proximal end of the middle piece) was frequently observed in the caput epididymides, whereas sperm in the corpus and cauda epididymides had normal morphology. Distribution of the peeled sperm changed as time passed and the corpus epididymides showed a peak incidence on D7. On D14, the highest incidence of abnormal sperm was observed in the cauda epididymides, where the major abnormality was tailless. Similar effects were also found in the 10mg/kg group but were less potent. Transmission electron microscopy of testicular sperm on D1 revealed the presence of elongated spermatids that lacked the mitochondrial sheath at the proximal end of the middle piece, although the round and elongating spermatids looked normal. These results suggest that DNOC exposure of male rats primarily causes partial loss of the mitochondrial sheath in the testicular elongated spermatids, and that the affected sperm become tailless by D14 after reaching the cauda epididymides.

A comprehensive evaluation of the testicular toxicity of dichlorvos in Wistar rats

Assessments of the reproductive toxicity of organophosphorus insecticides are important public health issues. This study aimed at defining the testicular toxicity of dichlorvos (DDVP) since this toxicity was suspected by our previous survey on pesticide sprayers and in some earlier publications during the 1970s. Ten-week-old Wistar rats were divided into four groups (n=8 or 9) and were injected subcutaneously with DDVP (0, 1, 2 or 4 mg/kg) 6 days a week for 9 weeks. After that period, erythrocyte cholinesterase (ChE) activities decreased dose-dependently, showing 44-55% inhibition among the treated groups. No significant difference was observed in the reproductive organ weights in any treated groups compared with the control group. Sperm motility decreased slightly but significantly in the 1 and 4 mg/kg groups, and significant regressions were observed between sperm motility and both blood ChE activity and urinary concentration of dimethyl phosphate (DMP), a urine metabolite of DDVP. However, sperm counts and sperm morphology in the cauda epididymidis, plasma testosterone concentrations, and histopathology in the testes in all the treated groups were not significantly different from those of the control group. Since only the sperm motility deteriorated by DDVP exposure at doses inducing marked inhibition of cholinesterase activities in the rats, it was suggested that the risk of testicular dysfunction posed to occupationally exposed humans would be small in terms of the effect of DDVP exposure alone. This conclusion was also supported by an estimate of the decrease in human sperm motility based on the urinary DMP concentrations observed in actual occupational settings.

Assessment of antifertility activities of abamectin pesticide in male rats

The effects of abamectin pesticide on fertility of adult male Sprague-Dawley rats were investigated. Adult male rats were exposed to tap water containing 0, 571, 857, or 1714 ppm abamectin for 6 weeks. Based on fluid consumption, animals received 0, 1.19, 1.87, and 2.13 mg/animal/day abamectin, respectively. Fertility was significantly reduced in male rats ingesting abamectin at all three doses in that the number of females impregnated by them was significantly reduced. The number of viable fetuses was significantly reduced in females mated with males that ingested abamectin at 1.87 or 2.13 mg/animal/day. Significant increases in the total number of resorptions and the number of females with resorptions were observed in females mated with the exposed males at all three concentrations. The body weight gain and water consumption were significantly lower in males that ingested 2.13 mg/animal/day abamectin. Likewise, ingestion of abamectin at all three concentrations caused a significant increase in the weight of testes. Epididymal and testicular sperm counts and daily sperm production were significantly decreased in exposed males. The serum level of testosterone was significantly reduced, whereas the serum level of follicle-stimulating hormone was significantly increased in males that ingested abamectin at a concentration of 2.13 mg/animal/day. Histological evaluation of the testes revealed several abnormalities including infiltration with congested blood vessels with marked hemorrhage and a significant accumulation of connective tissue surrounding the seminiferous tubules. These results strongly suggest the adverse effects of abamectin pesticide on male rat fertility.

Improved risk assessment by screening sperm parameters

The question of whether a 4 or 9 week premating treatment period is more suitable in studies for effects on fertility and early embryonic development, and the extent to which the screening of sperm parameters may contribute to the detection of effects, has been under discussion since the ICH guideline changed in 1994/1995. This study presents a comparison between 4 and 9 weeks treatment with known male reproductive toxicants with regard to sperm motility, count, morphology, abnormal movements and testicular and epididymal histopathology. Mating outcome was examined after 4 weeks treatment. Three compounds with different targets and mechanisms of action were chosen: two testicular toxicants, Pyridoxine and Adriamycin and the epididymal toxicant, alpha-Chlorohydrine. Sperm motility was reduced in males treated with Pyridoxine (markedly) and alpha-Chlorohydrine (slightly) after 4 weeks treatment and in males treated with Adriamycin after 9 weeks treatment. With Pyridoxine and Adriamycin, sperm count was significantly increased after 4 weeks. Histopathological examination after 4 weeks showed characteristic changes leading to marked testicular tubular atrophy at 8/9 weeks, which was confirmed by a significantly reduced sperm count at 8/9 weeks. With alpha-Chlorohydrine, sperm count was not affected and the results of the histopathological examination were equivocal. Changes in sperm morphology were observed after 4/9 weeks of treatment with Pyridoxine. Mating outcome after 4 weeks was markedly affected with both Pyridoxine and alpha-Chlorohydrine, but no effect was observed with Adriamycin. The results of this study indicate that the two testicular toxicants would have been detected as male reproductive toxicants in a 4-week general toxicity study with routine testicular histopathology and examination of sperm parameters, without the need for mating trials. For the epididymal toxicant, alpha-Chlorohydrine, there was slightly reduced sperm motility after 4 weeks treatment, but mating trials were necessary for confirmation of the toxic effect. Without sperm motility examination, this effect would have been missed in early drug development causing problems in clinical studies. Further comparisons of the validity of 4 or 9 weeks treatment require the testing of other compounds with different targets/mechanism of actions, as well as evaluation of dose-response relationships.

The vicinal chloroalcohols 1,3-dichloro-2-propanol (DC2P), 3-chloro-1,2-propanediol (3CPD) and 2-chloro-1,3-propanediol (2CPD) are not genotoxic in vivo in the wing spot test of Drosophila melanogaster

In this study, the vicinal chloroalcohols 1,3-dichloro-2-propanol (DC2P), 3-chloro-1,2-propanediol (3CPD) and 2-chloro-1,3-propanediol (2CPD) were investigated for genotoxicity in the wing spot test of Drosophila. DC2P is an important starting material in many processes of synthesis in chemical industry. 3CPD as well as some related glycerol chlorohydrins were identified in protein hydrolysates industrially used for the production of food items such as seasonings, sauces and soups. The wing spot test is a somatic mutation and recombination test (SMART) and is a sensitive in vivo assay for the detection of mutagens and promutagens. The test was applied here in its standard version with normal bioactivation and in a variant with increased cytochrome P450-dependent bioactivation capacity. All three compounds were clearly non-genotoxic in these in vivo assays. The results are in agreement with recent findings which strongly suggest that positive genotoxicity results in in vitro testing of vicinal chloroalcohols such as DC2P are due to directly acting genotoxic intermediates arising from a chemical reaction with the culture medium rather than from enzymatic biotransformation.

3-Chloro-2-hydroxypropylmercapturic acid and α-chlorohydrin as biomarkers of occupational exposure to epichlorohydrin

Until now no urinary biomarker of exposure was available to assess human exposure to epichlorohydrin (ECH). For this purpose the urinary excretion of mercapturic acids and α-chlorohydrin (α-CH), which are potential metabolites of ECH in humans was investigated. This study was undertaken in a chemical plant in which ECH is used in the production of glycidyl ethers. Urine samples were collected from 19 persons at the beginning and at the end of work-shifts and at the morning after the last work-shift. Respiratory air concentrations of ECH were determined by personal air monitoring (PAM) and were found to range from<0.03 to 1.1 mg/m(3) (8 h-TWA, median 0.09, n=23). The determined respiratory exposure to ECH was in all cases below the current occupational exposure limit of 4 mg/m(3) for ECH (8 h-TWA-OEL). In one additional case a dermal exposure to an unknown amount of technical ECH was noted. Urinary metabolites were isolated by ethyl acetate extraction or by lyophilization and determined by GC-MS. In ethyl acetate extracts of acidified urine samples of workers with potential occupational exposure to ECH, 3-chloro-2-hydroxypropylmercapturic acid (CHPMA) was identified with GC-MS and the concentrations measured ranged from<0.05 (detection limit) to 5.35 mmol/mol creatinine. The increase of the CHPMA excretion during the work-shifts, corrected for creatinine excretion, correlated well with the 8 h-TWA respiratory air concentrations of ECH (r(2)=0.94, n=7). For 8 individuals it was possible to assess an urinary half-life for the excretion of CHPMA (2.54±0.94 h). By extrapolating the relation between the ambient air concentrations of ECH and the urinary CHPMA excretions, an excretion of 6.2 mmol CHPMA/mol creatinine (tolerance levels of 95% C.I.: 5.1-7.3) is predicted if ECH exposure is at the level of the current OEL. The urinary excretion of two other known metabolites of ECH in rats, namely α-CH and 2,3-dihydroxypropylmercapturic acid (DHPMA) was also investigated. α-CH was identified in urine of workers exposed to low air concentrations of ECH but DHPMA could only be identified after the dermal exposure to technical ECH. In these latter samples CHPMA and α-CH were determined up to 167 and 6.3 mmol/mol creatinine, respectively. From this investigation it is concluded that urinary excretion of the mercapturic acid CHPMA is an appropriate biomarker of human exposure to ECH. A tentative biological exposure index (BEI) of 6 mmol CHPMA/mol creatinine for ECH during an 8 h work-shift is proposed.

Identification and quantitative determination of 3-chloro-2-hydroxypropylmercapturic acid and alpha-chlorohydrin in urine of rats treated with epichlorohydrin

Epichlorohydrin (ECH) is used in many industrial processes. Different toxic effects of ECH were found in rodents. The metabolism of ECH was investigated before in rats using [14C]ECH. The aim of this investigation was the development of non-radioactive quantitative analytical methods for measuring two urinary metabolites of ECH, namely 3-chloro-2-hydroxypropylmercapturic acid (CHPMA) and alpha-chlorohydrin (alpha-CH). The identity of CHPMA and alpha-CH excreted in urine of rats treated with 5 to 35 mg/kg ECH was confirmed by GC-MS. The quantitative analysis of CHPMA, involving ethyl acetate extraction from acidified urine and subsequent methylation and analysis by gas chromatography-flame photometric detection (GC-FPD), showed a method limit of detection of 2 micrograms/ml. The analysis of alpha-CH based on ethyl acetate extraction and subsequent analysis by GC-ECD, showed a method limit of detection of 2 micrograms/ml. CHPMA and alpha-CH derivatives could be determined quantitatively down to concentrations of 0.5 and 0.4 micrograms/ml urine, respectively, by selected-ion monitoring GC-MS under EI conditions. Cumulative urinary excretion of CHPMA and alpha-CH by rats treated with ECH were found to be 31 +/- 10 and 1.4 +/- 0.6% (n = 13) of the ECH dose, respectively. For CHPMA, the dose-excretion relationship suggested partially saturated ECH metabolism. For alpha-CH, the doe-excretion relationship was linear. With fractionated urine collection it was found that approximately 74 and 84% of the total cumulative excretion of CHPMA and alpha-CH, respectively, took place within the first 6 h after administration of ECH. From these investigations it is concluded that the GC-FPD and GC-ECD based methods developed are sufficiently sensitive to measure urinary excretion of CHPMA and alpha-CH in urine from rats administered 5 to 35 mg/kg ECH. It is anticipated that the analysis of CHPMA and alpha-CH based on GC-MS may be sufficiently sensitive to investigate urinary excretion from humans occupationally exposed to ECH.

Utilization of a short-term male reproductive toxicity study design to examine effects of alpha-chlorohydrin (3-chloro-1,2-propanediol)

alpha-Chlorohydrin (ACH) was administered to rats in a short-term male reproductive toxicity study to examine the usefulness of the method and to provide reference data with a substance that is known to elicit adverse effects on both sperm production and sperm quality within or following a 2-week treatment period. Adult male CD rats (10 per group) were administered ACH orally by gavage at doses of 0, 1, 5, or 25 mg/kg/day for 14 days. Males were killed on Test Day (TD) 15 or 29. A 2-week period without treatment was included to distinguish between testicular and posttesticular effects. At each time point, the reproductive system was evaluated by comparing testes weight, DNA ploidy distributions of testicular cell suspensions, testicular and epididymal histopathology, and epididymal sperm concentration, motility, morphology, and breakage. Beginning on TD 14, males to be killed on TD 29 were cohabited with untreated females (1:2). Females were killed on Gestation Day 13 and examined for pregnancy status. During the treatment period, minor depressions in body weight and relative food consumption occurred in rats administered 25 mg/kg ACH. Testicular and epididymal lesions also occurred at this dose level. DNA ploidy distributions determined by flow cytometry were predictive of testicular damage, with effects more pronounced on TD 29 than on TD 15. The preparation methods used selected for the most motile and vigorous population of epididymal sperm. Sperm motion was altered at the 5- and 25-mg/kg dose levels on TD 15. The percentage of motile sperm and the percentage of progressively motile sperm were markedly depressed at both the 5- and 25-mg/kg dose levels where antifertility effects occurred. Sperm velocities and amplitude of lateral head displacement were depressed at the 25-mg/kg dose level on both TD 15 and 29. Additionally, decreased epididymal sperm concentrations and increased breakage were recorded at this dose level. The findings in this study are consistent with the scientific literature for ACH and demonstrate posttesticular effects on epididymal sperm and delayed expression of testicular lesions. They also support the use of this methodology for an initial assessment of male reproductive effects.

Morphological and biochemical changes in the adult male rat reproductive system following long-term treatment with 1,2-dibromo-3-chloropropane

Adult Long-Evans male rats were treated with various dosages of pure or technical grade 1,2-dibromo-3-chloropropane (DBCP), epichlorohydrin (Epi), or allyl chloride (AC) for 1, 3, or 6 months on a daily basis. AC, which is the substrate for the production of DBCP, and Epi, which is a contaminant and/or metabolite of DBCP, had no effect on any of the parameters of the male reproductive system studied. The deleterious effects on male reproduction are therefore attributable specifically to DBCP. The effects of DBCP were dose and duration dependent. At the lowest dose (1 mg/kg) DBCP did not have any discernible effects on the male reproductive system. By 3 months of treatment at the intermediate dose of 5 mg/kg, the morphology of the testis ranged from normally appearing seminiferous tubules to ones which contained Sertoli cells only. At 6 months of treatment there was a reduction in the weights of the testes and sexual accessory glands. At the highest dose, the majority of the rats showed advanced testicular regression by 1 month of treatment. The most extreme testicular regression was observed in the 6-month treatment group. Almost all of the seminiferous tubules of all of the rats were composed of Sertoli cells only. In some of the animals, a few isolated seminiferous tubules contained an occasional spermatogonium or primary spermatocyte. Some of the Leydig cells of the rats in this group showed morphological evidence of atrophy as evidenced by the clumping of chromatin and paucity of stainable cytoplasm. This was confirmed by lower levels of intratesticular testosterone, a significant reduction in the number of luteinizing hormone (LH) receptors and increased serum levels of LH and follicle-stimulating hormone (FSH). From these results we conclude that DBCP is a specific male gonadotoxin and that the effects are not a result of contamination or metabolism. The effects appear to be a direct action at the testicular level because feedback inhibition to the pituitary gland was adversely affected.

Testicular damage development in rats injected with dibromochloropropane (DBCP)

Dibromochloropropane (DBCP) is an effective nematocide which was shown to suppress spermatogenesis and cause infertility in men and rats exposed to the compound. These damages were described only after 6-8 weeks post injection. The present study was set to detect the early development of the testicular damages. Rats were injected s.c. with DBCP 50 mg/kg. Control animals were injected with the vehicle alone (DMSO). Groups of animals were sacrificed 24 h, 1, 2, 3 and 4 weeks post injection. Body weight of DBCP treated animals was reduced from the second week post injection. Organs' weights of the DBCP treated rats, corrected for differences in body weights, were similar to those of controls. Four weeks post injection testes and accessory gland weights were significantly reduced as compared with controls. Percentage of damaged tubules in the DBCP treated animals were elevated from 16.6 +/- 3.5 at the first day to 70.2 +/- 6.4 at the 4th weeks. Concomitantly with the advance of tubular damage was a reduction in epididymal sperm count in the DBCP treated rats. One week post injection histological changes were evident. These included multinucleated giant cells and tubules blocked with sperm granuloma. It seems that alterations of spermatogenesis appear earlyer and are already noticeable one week post injection.

Testicular necrosis and DNA damage caused by deuterated and methylated analogs of 1,2-dibromo-3-chloropropane in the rat

To study the role of metabolism in 1,2-dibromo-3-chloropropane (DBCP)-induced testicular damage in rats, selectively deuterated and methylated analogs of DBCP were given as a single ip dose of 340 mumol/kg and testicular toxicity was determined 10 days after treatment. None of the four deuterated analogs C1-D2-, C2-D1-, C3-D2-, or C1-C2-C3-D5-DBCP reduced the degree of testicular damage compared to DBCP, indicating that metabolic cleavage of a C-H bond was not rate-limiting in DBCP-induced testicular toxicity. Of the five methylated analogs, C1-methyl-, C1-dimethyl-, C2-methyl-, and C3-methyl-DBCP and 1,2-dibromo-4-chlorobutane, only C3-methyl-DBCP caused testicular toxicity. DBCP treatment resulted in increased testicular DNA damage at doses of 85-170 mumol/kg as measured by alkaline elution of DNA from testicular cells isolated 3 hr after in vivo treatment. The perdeutero-DBCP analog induced testicular DNA damage that was at least as extensive as that induced by DBCP. Of the methylated analogs tested, only C3-methyl-DBCP gave a marked dose-dependent increase in testicular DNA damage between 170 and 540 mumol/kg. There were no significant differences in the testicular tissue distribution between DBCP, perdeutero-DBCP, and the methylated DBCP analogs. Furthermore, in distribution studies with DBCP, C1-methyl- and C3-methyl-DBCP, and 1,2-dibromo-4-chlorobutane, the highest tissue concentrations were found in the kidneys, followed by the liver and then the testes. The fact that testicular DNA damage of DBCP and its deuterated and methylated analogs paralleled their ability to cause testicular necrosis and atrophy makes measurement of DNA damage a very useful correlate in mechanistic studies of DBCP-induced testicular cell death.

Detection and mechanism of formation of the potent direct-acting mutagen 2-bromoacrolein from 1,2-dibromo-3-chloropropane

The nematocide 1,2-dibromo-3-chloropropane (DBCP) was converted to products which are mutagenic for Salmonella typhimurium TA 100 in the presence of rat liver microsomes, NADPH, and oxygen. Typical in vivo and in vitro inhibitors of cytochrome P-450 decreased DBCP mutagenicity in the presence of microsomes. Addition of glutathione to cytosolic preparations failed to bioactivate DBCP to mutagenic metabolites. Mutagenicity studies with selectively deuterated analogs showed that substitution of deuterium for hydrogen at C-1 or C-3 of DBCP modestly decreased mutagenicity, but that deuteration at both C-1 and C-3 markedly decreased mutagenicity. The formation rates of the potent direct-acting mutagen, 2-bromoacrolein (2-BA), in incubations of DBCP and its deuterated analogs with rat liver microsomes, correlated with the isotope effects on mutagenicity. Characterization of 2-BA was accomplished by gas chromatography-mass spectrometry using positive-ion chemical ionization. Mass spectral analysis of 2-BA formed from specifically deuterated analogs of DBCP indicated that initial oxidative dehalogenation at C-1 followed by a spontaneous beta-elimination reaction was the preferred pathway in the formation of 2-BA from DBCP. These results demonstrate that mutagenic metabolites of DBCP are formed by cytochrome P-450-mediated oxidative metabolism, and that 2-BA is a major mutagen formed.

Evidence that epichlorohydrin is not a toxic metabolite of 1,2-dibromo-3-chloropropane

The major urinary metabolite of 14C-epichlorohydrin, after oral administration to rats, was identified previously (Gingell et al. 1985) to be N-acetyl-S-(3-chloro-2-hydroxypropyl)-L-cysteine (ACPC) at 36% of the administered dose. In a similar study reported here, 1,2-dibromo-3-chloropropane (DBCP) was metabolized to at least 20 radioactive urinary metabolites. ACPC was only a minor metabolite (4%) of DBCP. Epichlorohydrin was metabolized in vitro by rat liver microsomes to alpha-chlorohydrin, but DBCP was not metabolized to epichlorohydrin or alpha-chlorohydrin under similar conditions. Covalent binding of radioactivity to liver microsomal proteins occurred for both substrates, but was less for 14C-epichlorohydrin than for 14C-DBCP. Addition of 3,3,3-trichloropropylene oxide, an inhibitor of epoxide hydrolase, increased the extent of protein binding of epichlorohydrin, but decreased the amount of 14C-DBCP which was bound. The data indicate the epichlorohydrin is not a significant in vivo nor in vitro metabolite of DBCP in the rat, and is unlikely to be responsible for the toxicity of DBCP.

Initial and residual toxicity following acute exposure of developing male rats to dibromochloropropane

Male Fischer 344 rats were given a single, sc injection of 1,2-dibromo-3-chloropropane (DBCP) at 6 or 25 days of age. One group of treated animals was killed 1 to 3 days afterward to compare the dose and time relationships of the acute toxic response of neonatal and weanling male rats to DBCP and another group at approximate sexual maturity (approximately 120 days of age) to detect residual toxic effects resulting from acute exposure. The 6-day-old rats were more susceptible than the 25-day-old rats to the acute toxic effects of DBCP, as characterized by reduced 48-hr survival, renal dysfunction, and renal and hepatic necrosis over the dose range of 80 to 320 mg/kg. The lowest dose tested, 20 mg/kg, and all higher doses reduced subsequent body and gonadal weight gains, and caused hypospermatogenesis or seminiferous tubular atrophy in animals exposed at 6 days of age and killed at sexual maturity. Similar effects were observed in animals exposed at 25 days of age, except that doses of 160 mg/kg or greater were required to produce residual toxic effects. These data indicate enhanced susceptibility of neonatal male rats to the gonadotoxic effects of dibromochloropropane, including the possibility of apparent irreversible injury caused by acute exposure.

1,2-dibromo-3-chloropropane (DBCP)-induced infertility in male rats mediated by a post-testicular effect

The potential for the chemosterilant 1,2-dibromo-3-chloropropane (DBCP) to reduce male fertility by acting at a site in the genital tract beyond the testis was evaluated in male, Fischer 344 rats. A single sc treatment with 100 mg/kg DBCP reduced fertility in male rats 2 to 7 days postexposure without affecting mating frequency. Doses of 10, 20, or 40 mg/kg DBCP given sc once daily for 7 days caused a dose-dependent reduction in the metabolism of glucose to CO2 by epididymal sperm, as measured in vitro. Conversion of glucose to lactate was not reduced, indicating inhibition of energy metabolism at a step post-glycolysis. No clinical signs of toxicity were observed in these studies. Direct addition of DBCP to epididymal sperm being incubated in vitro also inhibited the metabolism of glucose to CO2. Inhibition was concentration related, and the minimal inhibitory concentration was 0.316 mM. These data indicate that DBCP may cause a nearly immediate infertility via a direct effect on post-testicular sperm. A possible mechanism of this infertility is inhibition by DBCP of glucose metabolism in the ejaculated sperm.