Overview of reproductive and developmental toxicity studies of 1,3-butadiene in rodents

The Toxicological Properties of Petroleum Gases

To characterize the toxicological hazards of petroleum gases, 90-day inhalation toxicity (Organization for Economic Cooperation and Development [OECD] 413) and developmental toxicity (OECD 414) tests were conducted with liquefied propane gas (LPG) at concentrations of 1000, 5000, or 10 000 ppm. A micronucleus test (OECD 474) of LPG was also conducted. No systemic or developmental effects were observed; the overall no observed adverse effect concentration (NOAEC) was 10 000 ppm. Further, there was no effect of LPG exposure at levels up to 10 000 ppm on micronucleus induction and no evidence of bone marrow toxicity. Other alkane gases (ethane, propane, n-butane, and isobutane) were then evaluated in combined repeated exposure studies with reproduction/development toxicity screening tests (OECD 422). There were no toxicologically important changes in parameters relating to systemic toxicity or neurotoxicity for any of these gases at concentrations ranging from 9000 to 16 000 ppm. There was no evidence of effects on developmental or reproductive toxicity in the studies of ethane, propane, or n-butane at the highest concentrations tested. However, there was a reduction in mating in the high-exposure group (9000 ppm) of the isobutane study, which although not significantly different was outside the range previously observed in the testing laboratory. Assuming the reduction in mating to have been toxicologically significant, the NOAEC for the isobutane reproductive toxicity screening test was 3000 ppm (7125 mg/m3). A method is proposed by which the toxicity of any of the 106 complex petroleum gas streams can be estimated from its composition.

1,3-Butadiene: II. Genotoxicity profile

1,3-Butadiene’s (BD’s) major electrophilic metabolites 1,2-epoxy-3-butene (EB), 1,2-dihydroxy-3,4-epoxybutane (EBD), and 1,2,3,4-diepoxybutane (DEB) are responsible for both its mutagenicity and carcinogenicity. EB, EBD, and DEB are DNA reactive, forming a variety of adducts. All three metabolites are genotoxic in vitro and in vivo, with relative mutagenic potencies of DEB >> EB > EBD. DEB also effectively produces gene deletions and chromosome aberrations. BD’s greater mutagenicity and carcinogenicity in mice over rats as well as its failure to induce chromosome-level mutations in vivo in rats appear to be due to greater production of DEB in mice. Concentrations of EB and DEB in vivo in humans are even lower than in rats. Although most studies of BD-exposed humans have failed to find increases in gene mutations, one group has reported positive findings. Reasons for these discordant results are examined. BD-related chromosome aberrations have never been demonstrated in humans except for the possible production of micronuclei in lymphocytes of workers exposed to extremely high levels of BD in the workplace. The relative potencies of the BD metabolites, their relative abundance in the different species, and the kinds of mutations they can induce are major considerations in BD’s overall genotoxicity profile.

Ovarian follicle counts using proliferating cell nuclear antigen (PCNA) and semi-automated image analysis in rats

Ovarian follicle counting is a method to assess ovarian toxicity in reproductive toxicity studies in rats. Although ovarian follicle counting has been traditionally performed manually on hematoxylin and eosin (H&E)-stained sections, the use of immunohistochemical methods, including human cytochrome P450 1B1 (CYP1B1) and proliferating cell nuclear antigen (PCNA), have been used to enhance the visibility of the primordial and primary follicles to facilitate manual counting. In this study, serial sections from both ovaries from ten 3-month-old female Sprague Dawley rats were stained using routine H&E and immunohistochemistry for PCNA. Counting of primordial and primary follicles was performed manually using these two stains and by semi-automated image analysis of PCNA-stained slides. Although manual counting of PCNA-stained slides is preferable to manual counting of H&E-stained slides, manual counting involves variability between individual counters. Semi-automated image analysis of PCNA-stained slides yields an accurate and consistent count of these primordial/primary follicles and eliminates variability between individual counters.

DNA repair decline during mouse spermiogenesis results in the accumulation of heritable DNA damage

The postmeiotic phase of mouse spermatogenesis (spermiogenesis) is very sensitive to the genomic effects of environmental mutagens because as male germ cells form mature sperm they progressively lose the ability to repair DNA damage. We hypothesized that repeated exposures to mutagens during this repair-deficient phase result in the accumulation of heritable genomic damage in mouse sperm that leads to chromosomal aberrations in zygotes after fertilization. We used a combination of single or fractionated exposures to diepoxybutane (DEB), a component of tobacco smoke, to investigate how differential DNA repair efficiencies during the 3 weeks of spermiogenesis affected the accumulation of DEB-induced heritable damage in early spermatids (21-15 days before fertilization (dbf)), late spermatids (14-8dbf) and sperm (7-1dbf). Analysis of chromosomal aberrations in zygotic metaphases using PAINT/DAPI showed that late spermatids and sperm are unable to repair DEB-induced DNA damage as demonstrated by significant increases (P<0.001) in the frequencies of zygotes with chromosomal aberrations. Comparisons between single and fractionated exposures suggested that the DNA repair-deficient window during late spermiogenesis may be less than 2 weeks in the mouse and that during this repair-deficient window there is accumulation of DNA damage in sperm. Finally, the dose-response study in sperm indicated a linear response for both single and repeated exposures. These findings show that the differential DNA repair capacity of postmeiotic male germ cells has a major impact on the risk of paternally transmitted heritable damage and suggest that chronic exposures that may occur in the weeks prior to fertilization because of occupational or lifestyle factors (i.e., smoking) can lead to an accumulation of genetic damage in sperm and result in heritable chromosomal aberrations of paternal origin.

Toxicology of 1,3-butadiene, chloroprene, and isoprene

The diene monomers, 1,3-butadiene, chloroprene, and isoprene, respectively, differ only in substitution of a hydrogen, a chlorine, or a methyl group at the second of the four unsaturated carbon atoms in these linear molecules. Literature reviewed in the preceding sections indicates that these chemicals have important uses in synthesis of polymers, which offer significant benefits within modern society. Additionally, studies document that these monomers can increase the tumor formation rate in various organs of rats and mice during chronic cancer bioassays. The extent of tumor formation versus animal exposure to these monomers varies significantly across species, as well among strains within species. These studies approach, but do not resolve, important questions of human risk from inhalation exposure. Each of these diene monomers can be activated to electrophilic epoxide metabolites through microsomal oxidation reactions in mammals. These epoxide metabolites are genotoxic through reactions with nucleic acids. Some of these reactions cause mutations and subsequent cancers, as noted in animal experiments. Significant differences exist among the compounds, particularly in the extent of formation of highly mutagenic diepoxide metabolites, when animals are exposed. These metabolites are detoxified through hydrolysis by epoxide hydrolase enzymes and through conjugation with glutathione with the aid of glutathione S-transferase. Different strains and species perform these reactions with varying efficacy. Mice produce these electrophilic epoxides more rapidly and appear to have less adequate detoxification mechanisms than rats or humans. The weight of evidence from many studies suggests that the balance of activation versus detoxification offers explanation of differing sensitivities of animals to these carcinogenic actions. Other aspects, including molecular biology of the many processes that lead through specific mutations to cancer, are yet to be understood. Melnick and Sills (2001) compared the carcinogenic potentials of these three dienes, along with that of ethylene oxide, which also acts through an epoxide intermediate. From the number of tissue sites where experimental animal tumors were detected, butadiene offers greatest potential for carcinogenicity of these dienes. Chloroprene and then isoprene appear to follow in this order. Comparisons among these chemicals based on responses to external exposures are complicated by differences among studies and of species and tissue susceptibilities. Physiologically based pharmacokinetic models offer promise to overcome these impediments to interpretation. Mechanistic studies at the molecular level offer promise for understanding the relationships among electrophilic metabolites and vital genetic components. Significant improvements in minimization of industrial worker exposures to carcinogenic chemicals have been accomplished after realization that vinyl chloride caused hepatic angiosarcoma in polymer production workers (Creech and Johnson 1974; Falk et al. 1974). Efforts continue to minimize disease, particularly cancer, from exposures to chemicals such as these dienes. Industry has responded to significant challenges that affect the health of workers through efforts that minimize plant exposures and by sponsorship of research, including animal and epidemiological studies. Governmental agencies provide oversight and have developed facilities that accomplish studies of continuing scientific excellence. These entities grapple with differences in perspective, objectives, and interpretation as synthesis of knowledge develops through mutual work. A major challenge remains, however, in assessment of significance of environmental human exposures to these dienes. Such exposure levels are orders of magnitude less than exposures studied in experimental or epidemiological settings, but exposures may persist much longer and may involve unknown but potentially significant sensitivities in the general population. New paradigms likely will be needed for toxicological evaluation of these human exposures, which are ongoing but as yet are not interpreted.

Uterine-ovarian biochemical and developmental interactions to the postimplantation treatment with a butadiene metabolite, diepoxybutane, in pregnant rats

An industrial chemical used in synthetic rubber production, 1,3-butadiene, is toxic to reproduction in rats and mice. Bioactivation of butadiene to reactive intermediates, i.e. diepoxybutane and other metabolites, is responsible for this toxicity. The present study examines the biochemical and developmental mechanisms of diepoxybutane at the feto-maternal placental axis during gestation. Female Sprague-Dawley rats were administered four daily intraperitoneal doses of diepoxybutane in groups (0.25, 0.30, 0.35, or 0.40 mmol in sesame oil per kg body weight, n = 6/group) during postimplantation (gestation days 5-8) and euthanized on gestation day 9 or 12 for retrieval of uterine and ovarian tissues, and serum for assays. The results demonstrate that this timely diepoxybutane treatment significantly decreased placental levels of pituitary adenylate cyclase-activating polypeptide mRNA expression that was measured by reverse transcription-polymerase chain reaction and of matrix metalloproteinase-9 activity that was determined by gelatin zymography, and serum progesterone levels on gestation days 9 and 12. From a developmental standpoint, fetal growth and viability were reduced in correlation with treatment-related effects of diepoxybutane on implantation losses and fetal resorptions on gestation day 9. Additionally, fetal mortality was maximally increased due to significantly pronounced, dose-independent effects on these parameters on gestation day 12. This trend towards more severe embryolethal treatment effects from gestation day 9 to 12 suggests that fetal metabolism in the gravid uteri of rats may be more sensitive to diepoxybutane exposure as pregnancy progresses. The inhibitory actions of diepoxybutane on placental pituitary adenylate cyclase-activating polypeptide expression and matrix metalloproteinase activity may contribute towards altering placental molecular support for fetal development and viability. Moreover, the reproductive toxicity of diepoxybutane in rats appears to be linked to progesterone action.

Health risk assessment of 1,3-butadiene as a Priority Substance in Canada

1,3-Butadiene was included in the second list of Priority Substances to be assessed under the Canadian Environmental Protection Act. Potential hazards to human health were characterized on the basis of critical examination of available data on health effects in experimental animals and occupationally exposed human populations, as well as information on mode of action. Based on consideration of all relevant data identified as of April 1998, butadiene was considered highly likely to be carcinogenic to humans, and likely to be a somatic and germ cell genotoxicant in humans. In addition, butadiene may also be a reproductive toxicant in humans. Estimates of the potency of butadiene to induce these effects have been derived on the basis of quantitation of observed exposure-response relationships for the purposes of characterization of risk to the general population in Canada exposed to butadiene in the ambient environment.

Genetic and reproductive toxicity of butadiene and isoprene

Butadiene (BD) and its 2-methyl analogue, isoprene, have been extensively studied in animals and BD in population studies. Both chemicals are metabolised by liver cytochrome P450 dependent monogenases to monoepoxide and diepoxide intermediates. The diepoxide intermediates of both compounds were mutagenic in Salmonella typhimurium. However, unlike the monoepoxide of BD, the monoepoxides of isoprene were not mutagenic. It appears that they have no alkylating capacity. BD did not induce somatic cell mutation and recombination or sex-linked recessive lethal mutation in Drosophila melanogaster and isoprene produced no increase in chromosomal aberrations in CHO cells in vitro. Comparative concentrations of haemoglobin adducts in the blood of mice and rats after exposure to BD indicated that reaction with blood may decrease the levels of reactive intermediates available to tissues in rats, but not in mice contributing to greater potency of BD in the mouse. For isoprene, the adducts reach approximately the same concentrations in both species. DNA adducts have also been detected in testicular and lung cells of mice after BD exposure. The level of epoxybutene haemoglobin adducts was significantly elevated in BD-exposed workers, but lower than in rats and mice. In conjunction with the toxicology and carcinogenesis studies for BD and isoprene, additional mice were included for the evaluation of cytogenetic effects. Both chemicals produced increases in sister chromatid exchanges in bone marrow cells and in the frequency of micronuclei in normochromatic and polychromatic erythrocytes, but only BD produced an increase in the percent of bone marrow cells with chromosomal aberrations. At similar doses, the effects with BD were 2-3 times larger than with isoprene. There were also increased hprt mutation frequencies in rats and mice after BD exposure. Biomonitoring studies with hprt mutations in lymphocytes showed conflicting results, with both positive and negative findings. BD has been shown to be positive in one human cytogenetic biomonitoring study and not in three others, but chromosomal aberrations were increased in BD-exposed workers after challenge with gamma rays. Re-analysis of GSTTI null individuals showed positive results. There was an increase in spermatid micronuclei in mice by BD and its metabolites and in rats only by its metabolites. The cytotoxic response of germ cells in mice is greater than in rats. Dominant lethal mutations have been induced by BD and diepoxybutane, but not by epoxybutene. There was some evidence of congenital malformations in mice after BD exposure and there was a linear concentration-related induction of heritable translocations in mice. There was no induction of dominant lethal mutations or congenital malformations in rats. Using the heritable translocation data in mice, it has been determined that if a worker is continually exposed over 5 or 6 weeks to 20-25 ppm of BD, the risk of producing a child with a balanced reciprocal translocation is twice as high as the background risk. Since genetic damage cannot be measured directly in human germ cells, risk to such cells can also be estimated from germ cells and somatic cells of the mouse and human somatic cells using the parallelogram approach. Using doubling doses, the fourth corner of the parallelogram was calculated as a doubling dose for human germ cells of 4390 ppm/h. However, it is still questioned if man is more like rat than mouse in terms of sensitivity to exposure. Similar germ cell data do not exist for isoprene. In conventional developmental studies, where rats and mice were exposed to BD, maternal toxicity was shown in rats but there was no evidence of developmental toxicity or teratogenic effects and there was a small effect on sperm morphology. After exposure to isoprene, there was no adverse effect on rat dams or other reproductive indices. In mice, there was reduced foetal body weight and decreased maternal weight gain and isoprene also affected ovarian follicles. There was a reduction in testicular function parameters such as testicular weight and sperm motility.

A mechanistic assessment of 1,3-butadiene diepoxide-induced inhibition of uterine deciduoma proliferation in pseudopregnant rats

Butadiene diepoxide (BDE), a reactive metabolite of 1,3-butadiene that is an important industrial chemical used in synthetic rubber production causes a dose-dependent inhibition of deciduoma development in pseudopregnant Sprague-Dawley rats. This study used 4 daily i.p. BDE doses of 0.20, 0.25, 0.30, 0.35, or 0.40 to characterize mechanisms that may be responsible for the antideciduoma effect. Pseudopregnant rats were treated either before (pseudopregnancy [PPG] days 1-4) or after (PPG days 5-9) deciduoma induction by endometrial trauma with a blunt needle. Animals were killed on PPG day 9 and evaluated for serum progesterone and endometrial protein and DNA. RT-PCR was used to measure message for estrogen receptor (ER) alpha and pituitary adenylate cyclase-activating polypeptide (PACAP). Substrate zymography and Western blotting were used respectively to measure matrix metalloproteinase (MMP)-9 and inducible nitric oxide synthase. The antideciduoma effects of BDE were associated with decreases in endometrial weight, protein, and DNA, with decreases in serum progesterone, and with decreases in PACAP message and MMP-9. A reduction in NOS was identified at the highest dose of BDE. Message for estrogen receptor (ER) alpha was not affected at any dose. We conclude that the reduction in decidual proliferation was direct and appeared to be associated with either 1) a decrease in the effectiveness of the deciduogenic stimulation and/or a weakened endometrial sensitivity to the stimulus; or 2) an effect on deciduoma development. Molecular mechanisms that apparently contributed to BDE inhibition of decidual metabolism included the synthesis of protein and DNA involved in decidual growth, the synthesis and activation of a matrix metalloproteinase for degradation of the extracellular matrix that is essential for tissue remodeling during deciduoma development, and the nitric oxide/nitric oxide synthase and pituitary adenylate cyclase-activating peptide systems that are involved in promoting vasodilation and increased vascular permeability to enhance the availability of substrates for maximal deciduoma growth. The ovotoxicity of BDE, which has previously been established, may indirectly affect decidual proliferation by reducing progesterone, the preeminent endocrine regulator of deciduoma development. The findings also suggest that BDE may possess no estrogenic action since it was associated with endometrial weight loss and unaltered levels of the estrogen receptor alpha mRNA expression.

A review of the genetic and related effects of 1,3-butadiene in rodents and humans

In this paper, the metabolism and genetic toxicity of 1,3-butadiene (BD) and its oxidative metabolites in humans and rodents is reviewed with attention to newer data that have been published since the latest evaluation of BD by the International Agency for Research on Cancer (IARC). The oxidative metabolism of BD in mice, rats and humans is compared with emphasis on the major pathways leading to the reactive intermediates 1,2-epoxy-3-butene (EB), 1,2:3, 4-diepoxybutane (DEB), and 3,4-epoxy-1,2-butanediol (EBdiol). Results from recent studies of DNA and hemoglobin adducts indicate that EBdiol may play a more significant role in the toxicity of BD than previously thought. All three metabolites are capable of reacting with macromolecules, such as DNA and hemoglobin, and have been shown to induce a variety of genotoxic effects in mice and rats as well as in human cells in vitro. DEB is clearly the most potent of these genotoxins followed by EB, which in turn is more potent than EBdiol. Studies of mutations in lacI and lacZ mice and of the Hprt mutational spectrum in rodents and humans show that mutations at G:C base pairs are critical events in the mutagenicity of BD. In-depth analyses of the mutational spectra induced by BD and/or its oxidative metabolites should help to clarify which metabolite(s) are associated with specific mutations in each animal species and which mutational events contribute to BD-induced carcinogenicity. While the quantitative relationship between exposure to BD, its genotoxicity, and the induction of cancer in occupationally exposed humans remains to be fully established, there is sufficient data currently available to demonstrate that 1,3-butadiene is a probable human carcinogen.

Integrated defense system overlaps as a disease model: with examples for multiple chemical sensitivity

The central nervous, immune, and endocrine systems communicate through multiple common messengers. Over evolutionary time, what may be termed integrated defense system(s) (IDS) have developed to coordinate these communications for specific contexts; these include the stress response, acute-phase response, nonspecific immune response, immune response to antigen, kindling, tolerance, time-dependent sensitization, neurogenic switching, and traumatic dissociation (TD). These IDSs are described and their overlap is examined. Three models of disease production are generated: damage, in which IDSs function incorrectly; inadequate/inappropriate, in which IDS response is outstripped by a changing context; and evolving/learning, in which the IDS learned response to a context is deemed pathologic. Mechanisms of multiple chemical sensitivity (MCS) are developed from several IDS disease models. Model 1A is pesticide damage to the central nervous system, overlapping with body chemical burdens, TD, and chronic zinc deficiency; model 1B is benzene disruption of interleukin-1, overlapping with childhood developmental windows and hapten-antigenic spreading; and model 1C is autoimmunity to immunoglobulin-G (IgG), overlapping with spreading to other IgG-inducers, sudden spreading of inciters, and food-contaminating chemicals. Model 2A is chemical and stress overload, including comparison with the susceptibility/sensitization/triggering/spreading model; model 2B is genetic mercury allergy, overlapping with: heavy metals/zinc displacement and childhood/gestational mercury exposures; and model 3 is MCS as evolution and learning. Remarks are offered on current MCS research. Problems with clinical measurement are suggested on the basis of IDS models. Large-sample patient self-report epidemiology is described as an alternative or addition to clinical biomarker and animal testing.

Evaluation and characterization of micronuclei in early spermatids of mice exposed to 1,3-butadiene

The frequency of micronuclei induced in mouse meiotic cells after exposure to 1,3-butadiene has been evaluated in early spermatids. Germ cells were isolated from mice exposed to three butadiene concentrations (130, 250 and 500 ppm), at time intervals allowing to evaluate effects induced in late spermatocytes or at the stage of prelepotene/differentiating spermatogonia. The characterization of the origin of micronuclei, by simultaneous detection of centromeric and telomeric sequences, was also done on spermatid preparations from the 250 ppm concentration. The same analysis was carried out on a group of mice treated with the major butadiene metabolite, 1,2,3,4-diepoxybutane. The results obtained indicate a weak clastogenic effect of butadiene to premeiotic germ cells in the mouse.

Genetic effects of 1,3-butadiene on the mouse testis

1,3-Butadiene is a known male mouse germ-cell mutagen, to which humans may either be occupationally or environmentally exposed. Prolonged exposure to moderate or high doses in male mice can cause dominant lethal mutations and one report has indicated that 10 week inhalation administration of low doses can result in the production of malformed foetuses. The present study had dual purposes: (a) to attempt to clarify the suspected ability of sub-chronic (6 h/day, 5 days/wk, 10 weeks) low-dose exposure to 1,3-butadiene to induce heritable mutations in mouse male germ cells: (b) investigation of the relationships between testicular DNA damage, testicular DNA repair and foetal outcome. Adult male mice were exposed to low or moderate doses of 1,3-butadiene by inhalation sub-chronically or for a single 6 h period and either used for mating (sub-chronic exposure only) or for studies of DNA damage and repair. Litter size, dominant lethality and numbers of abnormal foetuses were determined the day preceding the normal day of parturition. Testicular DNA damage and repair were assessed by the Comet assay (for DNA damage) and the unscheduled DNA synthesis assay (for DNA repair). 1,3-Butadiene caused a statistically significant increase in dominant lethality at 125 ppm but not 12.5 ppm. No significant increase in DNA repair was found with either dose level or exposure period while only 6 h exposure to 125 ppm caused a small but significant increase in DNA damage as detected by the Comet assay. These effects demonstrate the reproductive genotoxicity of (125 ppm) 1,3-butadiene but do not confirm its ability to cause abnormalities in the offspring via the sperm. It is suggested that the relationship between 1,3-butadiene-induced DNA damage, DNA repair and heritable defects in the offspring may depend on the pattern of metabolites produced.

Genetic effects of 1,3-butadiene and associated risk for heritable damage

A summary of the results of the studies conducted in the EU Project "Multi-endpoint analysis of genetic damage induced by 1,3-butadiene and its major metabolites in somatic and germ cells of mice, rats and man" is presented. Results of the project are summarized on the detection of DNA and hemoglobin adducts, on the cytotoxic and clastogenic effects in somatic and germinal cells of mice and rats, on the induction of somatic mutations at the hprt locus of experimental rodents and occupationally exposed workers, on the induction of dominant lethal mutations in mice and rats, and on heritable translocations induced in mice, after exposure to butadiene (BD) or its major metabolites, butadiene monoepoxide (BMO), diepoxybutane (DEB) and butadiene diolepoxide (BDE). The primary goal of this project was to collect experimental data on the genetic effects of BD in order to estimate the germ cell genetic risk to humans of exposure to BD. To achieve this, the butadiene exposure are based on data for heritable translocations and bone marrow micronuclei induced in mice and chromosome aberrations observed in lymphocytes of exposed workers. A doubling dose for heritable translocations in human germ cells of 4900 ppm/h is estimated, which, assuming cumulative BD exposure over the sensitive period of spermatogenesis, corresponds to 5-6 weeks of continuous exposure at the workplace to 20-25 ppm. Alternatively, the rate of heritable translocation induction per ppm/h of BD exposure is estimated to be approximately 0.8 per million live born, compared to a spontaneous incidence of balanced translocations in humans of approximately 800 per million live born. These estimates have large confidence intervals and are only intended to indicate orders of magnitude of human genetic risk. These risk estimates are based on data from germ cells of BD-exposed male mice. The demonstration that clastogenic damage was induced by DEB in preovulatory oocytes at doses which were not ovotoxic implies that additional studies on the response of mammalian female germ cells to BD and its metabolites are needed. The basic assumption of the above genetic risk estimates is that experimental mouse data obtained after BD exposure can be extrapolated to humans. Several points exist in the present report and in the literature which contradict this assumption: (1) the level of BMO-hemoglobin adducts was significantly elevated in BD-exposed workers; however, it was considerably lower than would have been predicted from comparable rat and mouse exposures; (2) the concentrations of the metabolites DEB and BMO were significantly higher in mouse than in rat blood after BD exposure. Thus, while metabolism of BD is qualitatively similar in the two species, it is quantitatively different; (3) no increase of HPRT mutations was shown in 19 workers exposed on average to 1.8 ppm of BD, while in a different population of workers from a US plant exposed on average to 3.5 ppm of BD, a significant increase of HPRT variants was detected; and (4) data from cancer bioassays and cancer epidemiology suggest that rat is a more appropriate model than mouse for human cancer risk from BD exposure. However, the dominant lethal study in rats gave a negative result. At present, we do not know which BD metabolite(s) may be responsible for the genetic effects even though the bifunctional alkylating agent DEB is the most likely candidate for the induction of clastogenic events. Unfortunately, methods to measure DEB adducts in hemoglobin or DNA are only presently being developed. Despite these several uncertainties the use of the mouse genetic data is regarded as a justifiable and conservative approach to human genetic risk estimation given the considerable heterogeneity observed in the biotransformation of BD in humans.

A comparison of male-mediated effects in rats and mice exposed to 1,3-butadiene

There is current concern that exposure of men to certain agents such as radiation and smoking can adversely affect their offspring in terms of cancer outcome. Studies in laboratory animals after radiation have supported such an association, and other studies after male exposure to radiation and various chemicals have also resulted in congenital malformations. The present study was undertaken to examine congenital malformations in offspring from males exposed to 1,3-butadiene over a lower dose range than that in an earlier mouse study and to determine if there was a species difference in sensitivity between rats and mice. An earlier extended dominant lethal study of male CD-1 mice exposed by inhalation to 12.5 ppm and 1250 ppm of 1,3-butadiene for 6 h/day, 5 days/wk, for 10 weeks produced an increase in F1 abnormalities and late deaths at 12.5 ppm and in early deaths at 1250 ppm. The present study examined the same reproductive effects after exposure of male CD-1 mice for 6 h/day, 5 days/wk, for 4 weeks to 12.5, 65 and 130 ppm of 1,3-butadiene. There was no increase in early deaths at 12.5 ppm as in the earlier study but there were statistically significant increases in early deaths at 65 and 130 ppm study and these were not dose-related. There was a non-significant increase in F1 gross abnormalities at 130 ppm and no increase in late deaths. The present study also examined male Sprague-Dawley rats after exposure to 65,400 and 1250 ppm for 6 h/day, 5 days/wk, for 10 weeks. There were no effects on early deaths, late deaths, or congenital malformations in the rat study. There was a reduction in implants at 65 ppm but this was not considered to be biologically/genetically significant as there was no corresponding increase in early deaths and the response was not dose-related. The differences observed between the rat and mouse studies would confirm the greater sensitivity to 1,3-butadiene of the mouse by comparison with the rat as reported by other workers for other parameters.

Somatic and germ cell effects in rats and mice after treatment with 1,3-butadiene and its metabolites, 1,2-epoxybutene and 1,2,3,4-diepoxybutane

1,3-Butadiene is produced in large quantities for use in the manufacture of synthetic rubber. It is also an environmental pollutant. There is concern about exposure to 1,3-butadiene as it has been shown to produce tumours in rats, mice and an increased risk of leukaemia in humans. It has also been shown to produce germ cell effects in mice. Differences in responses to 1,3-butadiene have been reported in rats and mice, possibly due to different metabolic capabilities. The present study thus investigated somatic and germ cell effects of 1,3-butadiene in mice and its metabolites in both rats and mice to help determine species differences using different endpoints for genotoxic effects. These included DNA strand breakage as measured in the single cell gel electrophoresis (Comet assay) in bone marrow and testicular cells, and micronuclei in bone marrow cells using both the acridine orange and Giemsa staining methods. Unscheduled DNA synthesis (UDS) was also measured in the testes of mice. CD-1 mice were exposed to 1,3-butadiene by inhalation for 6 h/day for 4 weeks, and CD-1 mice and Sprague-Dawley rats to the metabolites after i.p. injection. 1,3-Butadiene did not affect liver, bone marrow and testicular cells in mice as measured in the Comet assay. After treatment with 1,2-epoxybutene in the Comet assay, there was a response in the testes in mice but not in rats and there was little or no effect in the bone marrow assay in mice but there was in rats. After treatment with 1,2,3,4-diepoxybutane in the Comet assay in mice, there was a response in the bone marrow cells but not in the testicular cells, and in rats there was also a response only in bone marrow cells. There was an increase in micronuclei in both rats and mice with both metabolites, but clastogenicity was stronger with 1,2,3,4-diepoxybutane, occurring at lower doses, than with 1,2-epoxybutene. In the UDS assay in the testes of mice, there was an increase in response with 1,2,3,4-diepoxybutane treatment but not with 1,2-epoxybutene. These studies would appear to confirm a species difference of CD-1 mice and Sprague-Dawley rats, where mice were sensitive at lower doses than rats.

Micronucleus induction in germ and somatic cells of the mouse after exposure to the butadiene metabolites diepoxybutane and epoxybutene

The genotoxicity of diepoxibutane (DEB) and epoxybutene (EB), two of the main metabolites of 1,3-butadiene, was tested in the germ and somatic cells of the mouse by applying an MN assay in early spermatids, and in peripheral blood reticulocytes of a subgroup of the same animals. DEB (0.17 and 0.35 mmol/kg) and EB (0.35, 0.70 and 1.04 mmol/kg) were administered i.p. In the germ cell assay, significant increases of MN were observed after treatment of premeiotic S-phase cells with both butadiene metabolites, but DEB was shown to be more powerful than EB in the induction of chromosomal damage. A weak effect of the same compounds was also found after treatment of late spermatocytes, approaching the meiotic divisions. From the MN assay in peripheral blood reticulocytes, a statistically significant increase of the frequency of MN was detected at each dose tested for both chemicals. However, the results have again shown that DEB is much more efficient than EB in inducing chromosome damage.

Germ cell mutagenicity of three metabolites of 1,3-butadiene in the rat: induction of spermatid micronuclei by butadiene mono-, di-, and diolepoxides in vivo

Three metabolites of the industrial chemical 1,3-butadiene (BD), namely butadiene monoepoxide (BMO, 3,4-epoxy-1-butene), diepoxide (DEB, 1,2;3,4-diepoxybutane), and diolepoxide (DE, 3,4- epoxybutane-1,2-diol) were studied for germ cell mutagenicity using the rat spermatid micronucleus (MN) test. All three epoxides increased slightly, but significantly, the frequency of spermatid MN. The most sensitive stage to the action of BMO and DEB was preleptotene (meiotic S phase) harvested at 18-day time intervals after treatment. The dose-response for BMO followed a second order curve at this time interval, with maximum MN induction at the dose of 186 mumol/kg and lower induction of higher doses. Late stages of the meiotic prophase (late pachytene-diplotene-diakinesis) also showed some sensitivity to the three epoxides. Stem cell spermatogonia were affected by DEB as observed by a slight induction of spermatid micronuclei 50 days after treatment. No clear cytotoxic effects were observed by measuring testicular weight or cell numbers of seminiferous epithelial stage 1 18 days after the treatments. DEB at the dose 387 mumol/kg caused a slight inhibition of spermatogonial DNA synthesis in stage I and a delay of meiotic DNA replication observed in stage XII 72 hr after treatment. Since BMO is able to induce spermatid MN in the rat, the present results, together with previous data, indicate that rat bone marrow MN results that are negative for both BD and BMO cannot directly predict mutagenicity in male germ cells. The results also emphasize that tissue; species, and strain-specific differences in metabolism have to be taken into account when the genetic risks of human butadiene exposure are evaluated. The results support the conclusion that 1,3-butadiene is a germ cell mutagen-possibly also in humans.

Review of reproductive and developmental toxicity of 1,3-butadiene

Toxic doses of 1,3-butadiene (BD) have been reported to cause reproductive and/or developmental toxicity. Regardless of the strain used, mice were always affected by BD at lower doses than rats, an expected observation, based on well recognized differences in pharmacokinetic (PK) parameters in these two species. Because the mouse is particularly sensitive to BD in comparison with other laboratory species, and there are important functional and anatomical differences between humans and mice, the NOELs and LOELs identified for BD for various reproductive endpoints in mice may not be relevant to human reproductive risk. In mice, the LOELs for reproductive endpoints include developmental toxicity at 200 ppm, genotoxic effects at 500 ppm (mouse spot test), ovarian atrophy in females at 6.25 ppm (carcinogenicity study), reduced testicular weights at 200 ppm and testicular atrophy at 625 ppm BD in males (carcinogenicity studies), low incidences of abnormal sperm heads at 1000 and 5000 ppm BD (sperm head morphology study), small reversible increases in resorption at 1250/1300 ppm or 5000 ppm (dominant lethal studies), and other possible sequelae of genotoxicity resulting from exposure of male mice at 12.5 ppm BD and higher (dominant lethal study). When available, the much higher NOELs and LOELs of other species tested for the same endpoints should be considered. For example, maternal and developmental NOELs for BD in the rat were 200 and 1000 ppm, respectively, and 40 ppm in the mouse. Likewise, exposure of cohabited pairs of rats, guinea pigs and rabbits or of female dogs to BD concentrations as high as 6700 ppm for 8 months did not impair fertility or cause testicular or ovarian atrophy in these species. Thus, consideration of these remarkable species-dependent differences in toxicity is necessary. In addition, there are alternative scientific interpretations for some of the mouse studies and this review attempts to address these areas. For example, it may be incorrect to categorize results indicating weak in vivo genotoxic effects in male mice (sperm head morphology and dominant lethal studies) at 12.5 ppm BD and higher as reproductive effects because concentrations of BD as high as 5000 ppm did not affect mating, fertility or live litter sizes, even in this sensitive species. Similarly, it may be inappropriate to identify the ovary as a target organ for reproductive risk since the ovarian atrophy in mice was identified after completion of the normal reproductive life and after more than 15 months of exposure. Neither ovarian nor testicular atrophy occurred in Sprague-Dawley rats after exposure to BD concentrations as high as 8000 ppm for 105 (females) or 111 (males) weeks.

Male-mediated F1 effects in mice exposed to 1,3-butadiene

We examined the effects on dominant lethality, the incidence of fetal abnormalities and tumour incidence in surviving offspring of acute and subchronic exposure of male mice by inhalation to the industrial monomer, 1,3-butadiene. In the acute study, CD-1 mice were exposed to atmospheres containing 0 (n = 25), 1250 (n = 25) or 6250 ppm (n = 50) for 6 h, and each male was caged 5 days later for 1 week with two untreated virgin females. One of the females was killed humanely on day 17 of gestation. The other was allowed to deliver and rear her litter and the litters were monitored throughout adulthood. The killed female was examined for the number of live foetuses, the number of post implantation deaths (early and late) and the number and type of any gross malformations. In the subchronic study, males were exposed to 0 (n = 25), 12.5 (n = 25) or 1250 (n = 50) for 6 h per day on 5 days per week for 10 weeks and then mated the next morning. Mating and observation details were as for the acute study. Acute exposure to butadiene resulted in only a small decrease in implantations; after 10 weeks' subchronic exposure with either the high or low concentration, however, a wide variety of statistically significant effects was seen. At 1250' ppm, the number of implantations was reduced, dominant lethal mutations were induced, and the incidences of early and late deaths were increased; some of the live foetuses were malformed. The low dose also increased the frequency of malformations and late deaths but it did not affect the number of early deaths. Skeletal examination of malformed foetuses, randomly selected normal litter mates and controls confirmed the abnormalities seen at necropsy in malformed foetuses. However, karyotypic analysis of foetal liver from malformed foetuses, randomly selected normal litter mates and controls showed no karyotypic abnormalities. The number of gross suspected tumours in the F1 adults did not appear to reveal an increase over control values. Thus, butadiene is mutagenic in the germ cells of male mice, as shown by the induction of dominant lethality at 1250 ppm, and the frequencies of late deaths and congenital malformations appear to be increased at the subchronic level of 12.5 ppm and skeletal examination of malformed foetuses confirmed the macroscopic abnormalities.

Synthesis report of the step project detection of germ cell mutagens

The project 'Detection of Germ Cell Mutagens' was designed with three major goals: (1) Detection and characterization of germ-cell mutagens; (2) standardization and validation of new germ-cell tests; and (3) development of a data base on germ-cell mutagenicity. All three goals were achieved. The classical germ-cell tests were applied to characterize the genetic effects of acrylamide (AA), 1,3-butadiene (BD), trophosphamide (TP) and urethane (UR). All but UR were found to cause heritable genetic damage. The experimental data obtained for AA and BD were the basis for genetic risk evaluations during the EC/US Workshop on Risk Assessment 'Human Genetic Risk from Exposure to Chemicals, Focusing on the Feasibility of the Parallelogram Approach'. Nine chemicals were employed to validate the spermatid micronucleus assay with mice and rats: AA, BD and its metabolites 1,2-epoxybutene-3 and 1,2:3,4-diepoxybutane, chlorambucil, mitomycin C, methylnitrosourea, TP and UR. The spermatid micronucleus test was combined with micronucleus tests in somatic cells such as bone marrow or peripheral blood erythrocytes, and splenocytes which allowed a comparison of effects in somatic and germinal cells. Improvements of the spermatid micronucleus test included BrdU-labelling of premeiotic S-phase for the determination of stage sensitivity and fluorescence in situ hybridization with pancentromeric DNA-probes to distinguish between clastogenic and aneugenic events. The results indicate that the spermatid micronucleus test with its improvements is an adequate procedure to detect germ-cell clastogenicity and to compare the activity of chemicals in different tissues and between species, i.e., rats and mice. Other germ cell methods under study were the flow cytometric measurement of testicular sperm DNA and the cytogenetic analysis of preimplantation embryos for chromosomal aberrations and micronuclei. The collection of a reliable germ-cell data base was accomplished through a critical evaluation of the literature and with the data obtained in the present project. Remarkable concordance between responses of germ cell tests to chemical mutagens was the most striking conclusion to be drawn from the present data base.

1,3-Butadiene working group report

During the Workshop in North Carolina, the in vivo metabolism, adduct formation and genotoxicity data available from rodent and human exposure to 1,3-butadiente (BD) were reviewed and they are summarized in the present report. BD is metabolized by cytochrome P-450-dependent monoxygenases to the primary metabolite 1,2-epoxybutene-3 (epoxybutene, EB). EB is subjected to further metabolism: oxidation to 1,2:3,4-diepoxybutane (DEB), hydrolysis to 3-butene-1,2-diol and conjugation to glutathione. The first pathway seems to prevail in mice while the latter is characteristic for rats and possibly for humans. Species differences exist in adduct formation of the monoepoxide to hemoglobin, for which the following pattern has been found: mice > rats > humans. Genotoxity of BD was found in mice with all applied tests; however, negative results were obtained in rats. In exposed humans, the cytogenetic studies in peripheral blood lymphocytes did not show genotoxic effects, although one report described elevated hprt variant levels in peripheral blood lymphocytes of exposed workers. It was concluded that the presently available data are insufficient for the application of the parallelogram model to estimate genetic risk for humans. As an alternative approach, a tentative estimate of the doubling dose for induction of hprt mutations in somatic cells of mice and men was performed and the calculated values were surprisingly similar, i.e. 9000 ppmh. However, this estimate is burdened with a number of caveats which were discussed in detail. The working group identified a series of urgent research needs to provide the appropriate data for the application of the parallelogram model, such as identification of metabolic pathways in different rodent species and humans, metabolic studies in mice, rats and humans considering metabolic polymorphisms, studies of adducts to DNA and hemoglobin especially of DEB and other butadiene metabolites in rodents and humans, studies of mutational spectra (mutational fingerprinting) in somatic and germinal cells, confirmation of the human hprt mutation data, conformation of the rodent malformation data, dose-response studies in rodent germ cell tests and studies on repair kinetics of mono-adducts induced by EB as opposed to repair of cross-links produced by DEB. Finally, it was suggested that the original parallelogram consisting of data from somatic cell studies in rodents and humans plus studies of heritable effects in rodents to extrapolate to germ cell risk for humans should be supplemented with studies in sperm of experimental animals and exposed men.

Heritable translocations induced by inhalation exposure of male mice to 1,3-butadiene

Previously, we reported that dominant lethal mutations were induced in spermatids after inhalation exposure of male (102/El x C3H/El)F1 mice to 1300 ppm of 1,3-butadiene on 5 days for 6 h per day (exposure dose 39,000 ppm h). The same inhalation exposure was given to male C3H/El inbred mice which were mated to inbred line 102/El females 8-14 d after the end of exposure. Male and female F1 hybrid progeny were tested for the presence of heritable translocations by observation of litter sizes and by cytogenetic analyses in meiotic and somatic cells. 1,3-Butadiene induced heritable translocations in late spermatids. The translocation frequency after 1,3-butadiene exposure to 39,000 ppm h was 2.7% (16 translocation heterozygotes among 559 F1 offspring). This frequency is 54 times higher than the historical control frequency (0.05%; 5 translocation heterozygotes among 9500 F1 offspring). Thus, 1,3-butadiene causes heritable germ cell effects in mice.

Clastogenic effects of 1,3-butadiene and its metabolites 1,2-epoxybutene and 1,2,3,4-diepoxybutane in splenocytes and germ cells of rats and mice in vivo

Clastogenicity of 1,3-butadiene (BD), 1,2-epoxybutene (EB), and 1,2,3,4-diepoxybutane (DEB) was studied in splenocytes and germ cells of rats and mice by means of micronucleus assays (cytokinesis-block method for splenocytes, suspension method for germ cells). Inhalation exposure of mice to 200, 500, or 1,300 ppm BD (6 h/d; 5 days) induced significant chromosome damage in spermatocytes at the preleptotene stage. EB and DEB induced significant amounts of clastogenic damage in splenocytes and spermatocytes of rats and mice. The lowest tested effective doses for mice and rats were, respectively, 40 and 80 mg/kg for EB, and 15 and 30 mg/kg for DEB. In splenocytes, 80 mg EB/kg induced 3.6 times more MN in mice than in rats, whereas 30 mg DEB/kg induced the same amount of damage in both species. Damage in germ cells of mice was induced in early spermatocytes treated with 40 and 80 mg EB/kg, and in late spermatocytes exposed to 30 mg DEB/kg. In rats, 40 mg EB/kg induced damage in early spermatocytes, whereas 80 mg EB/kg induced chromosomal damage in early and late spermatocytes. In rats treated with DEB, clastogenic damage was induced in spermatocytes at preleptotene, zygotene, diplotene, and diakinesis stages. When the clastogenic potential of EB and DEB in splenocytes and germ cells of mice and rats was compared, DEB always showed a stronger effect than EB. Body weight, testis weight, ratio of testis weight to body weight, and ratio of Golgi to Golgi + cap phase spermatids were used as parameters for toxicity. Exposures to 500 and 1,300 ppm BD were somewhat toxic to mice. Doses of 80 mg EB/kg and 30 mg DEB/kg exhibited toxic effects in mice and rats.

Mutagenicity of 1,3-butadiene inhalation in somatic and germinal cells of mice

Inhalation exposure of mice to 50, 200, 500 or 1300 ppm of 1,3-butadiene for 6 h per day for 5 consecutive days caused micronuclei in mouse bone marrow and peripheral blood erythrocytes. The dose response was non-linear. The slope of the curve flattened with increasing exposure concentration. Coat color spots were found in the mouse spot test after exposure of pregnant females on pregnancy days 8-12 to 500 ppm of 1,3-butadiene. Dominant lethal mutations were induced in spermatozoa and late spermatids after exposure of male mice to 1300 ppm with the 5-day exposure regimen. Thus, in the mouse 1,3-butadiene is a somatic and germ cell mutagen.

Dominant lethal effects after inhalation exposure to 1,3-butadiene

Two independent dominant lethal experiments were performed using different protocols with respect to strains of mice, inhalation exposure duration of 1,3-butadiene, and mating regimen. The short communication summarizes the results of the experiments and compares the induced dominant lethality according to the formula published by Ehling in 1978. Despite the differences in methodology the results are in close agreement. The sum of the dominant lethal effects observed during the first three mating weeks after 1 week of butadiene exposure in one experiment (23.1%) is surprisingly similar to the dominant lethal effect observed during 1 week of mating after 10 weeks of butadiene exposure (28.1%) in the other experiment. The results of the two independent experiments strengthen the conclusion that butadiene is a germ cell mutagen. Furthermore, the results indicate that the effect observed after 10 weeks of exposure is representative of the last three treatment weeks, i.e. treated spermatozoa and spermatids.

A brief survey of butadiene health effects: a role for metabolic differences

1,3-Butadiene is a major monomer in the rubber and plastics industry and is one of the highest-production industrial chemicals in the United States. Although not highly acutely toxic to rodents, inhalation of concentrations as low as 6.25 ppm causes tumors in mice. Butadiene is oncogenic in rats, but much higher exposure concentrations are required than in mice. Chronic toxicity targets the gonads and hematopoietic system. Butadiene is also a potent mutagen and clastogen. Differences in the absorption, distribution, and elimination of butadiene appear to be relatively minor between rats and mice, although mice do retain more butadiene and its metabolites after exposure to the same concentration and have a higher rate of metabolic elimination. Recent studies have demonstrated that major species differences appear to occur in the rate of detoxication of the primary metabolite, 3-epoxybutene (butadiene monoepoxide [BDMO]). Mice have the greatest rate of production of BDMO as compared to other species, but the rate of removal of BDMO appears to be less than in other species. Mice have low levels of epoxide hydrolase; rats have intermediate levels; monkeys and humans appear to have high levels of this detoxifying enzyme. Thus, while only low levels of butadiene exposure may result in an accumulation of BDMO in the mouse, much higher levels would be required to result in an elevation of circulating BDMO in other species. The level of this reactive metabolite may be correlated with the species differences in butadiene sensitivity.

Developmental toxicology: status of the field and contribution of the National Toxicology Program

The NTP has conducted developmental toxicity studies on more than 50 chemicals, often in multiple species. Several chemicals caused developmental toxicity in the absence of any toxicity to the mother. Although hazard to humans is determined by the level of exposure to the chemical and its inherent toxicity, those agents that selectively disturb the development of the conceptus are of particular concern because other manifestations of toxicity would not warn the mother of overexposure. Whether the LOAEL (lowest-observed adverse effect level) for maternal toxicity was high or low did not correlate with the potential of chemicals to cause developmental toxicity. The form of developmental toxicity that determined the LOAEL most frequently was decreased body weight in mice and rats, but not rabbits, where the LOAEL was determined more often by an increase in resorptions. Several in vitro and short-term tests appear promising as screens to predict the outcome of developmental toxicity studies in mammals. However, the only screens that have undergone formal validation studies are those evaluated by the NTP. Improvements in our ability to predict risk to humans have been limited by our knowledge of the mechanisms by which agents cause developmental toxicity. Thus, future growth is dependent on a better understanding of the biological processes that regulate normal development, therein providing the necessary framework for understanding mechanisms of abnormal development.

Dangerous and cancer-causing properties of products and chemicals in the oil refining and petrochemical industry--Part II: Carcinogenicity, mutagenicity, and developmental toxicity of 1,3-butadiene

1,3-butadiene (BD) is present in synthetic rubber and motor fuels (gasoline). BD is shown to cause lymphocytic lymphomas, heart hemangiosarcomas, lung alveolar bronchiolar cancers, forestomach-squamous cell cancers, harderian gland neoplasms, preputial gland adenoma or carcinoma, liver-hepatocellular cancers, mammary gland acinar cell carcinomas, ovary-glanulosa cell carcinoma, brain cancers, pancreas adenoma and carcinoma, testis-Leydig cell tumors, thyroid follicular adenoma and carcinoma, and zymbal gland carcinoma in rodents and to date no exposure level has been established at which this chemical does not cause cancers. In humans BD causes increase in lymphomas, leukemias, and other cancers of hematopoietic systems and organs. BD is also a potent alkylating agent, directly toxic to developing embryos and damages progeny after parental exposure.