Micronuclei, DNA single-strand breaks and DNA-repair activity in mice exposed to 1,3-butadiene by inhalation

We investigated single-strand breaks and endonuclease III-sensitive sites in DNA along with gamma-irradiation-specific DNA-repair activity in hepatocytes and frequencies of micronuclei in polychromatic bone-marrow erythrocytes of male NMRI mice (2 months old, weight 30-35 g) during sub-acute inhalation exposure to 1,3-butadiene (28 days, 500 mg/m3) and up to 28 days after the exposure. Concentrations of 1,3-butadiene in blood, an indicator of internal exposure, moderately increased during the exposure period. The most interesting finding was that gamma-irradiation-specific DNA-repair activity gradually increased during exposure, being significantly higher compared with control levels on days 7 and 28 of exposure (P = 0.005 and 0.035, respectively), reaching a maximum on day 1 after the termination of exposure (P = 0.003) and then returning to control levels. A significant correlation between gamma-irradiation-specific DNA-repair activity and the concentration of 1,3-butadiene in blood (R = 0.866, P = 0.050) supports a possible induction of DNA-repair activity by the exposure to 1,3-butadiene and formation of its metabolites. The initial increase in micronucleus frequency (micronuclei per 1000 cells) in the exposed mice continuously decreased from 20.4 +/- 5.1 (day 3) to 15.1 +/- 3.2 (day 28) within the exposure period, and subsequently from 12.4 +/- 5.1 to 4.6 +/- 1.6 in the period following termination of the 1,3-butadiene exposure, while micronucleus frequencies in control animals were significantly lower (from 1.7 +/- 1.5 to 4.2 +/- 0.8).     

Dose responses for DNA adduct formation in tissues of rats and mice exposed by inhalation to low concentrations of 1,3-[2,3-[(14)C]-butadiene

Male Sprague-Dawley rats and B6C3F1 mice were exposed to either a single 6h or a multiple (5) daily (6h) nose-only dose of 1,3-[2,3-(14)C]-butadiene at exposure concentrations of nominally 1, 5 or 20 ppm. The aim was to compare the results with those from a similar previous study at 200 ppm. DNA isolated from liver, lung and testis of exposed rats and mice was analysed for the presence of butadiene related adducts, especially the N7-guanine adducts. Total radioactivity present in the DNA from liver, lung and testis was quantified and indicated more covalent binding of radioactivity for mouse tissue DNA than rat tissue DNA. Following release of the depurinating DNA adducts by neutral thermal hydrolysis, the liberated depurinated DNA adducts were measured by reverse phase HPLC coupled with liquid scintillation counting. The guanine adduct G4, assigned as N7-(2,3,4-trihydroxybutyl)- guanine, was the major adduct measured in liver, lung and testis DNA in both rats and mice. Higher levels of G4 were detected in all mouse tissues compared with rat tissue. The dose-response relationship for the formation of adduct G4 was approximately linear for all tissues studied for both rats and mice exposed in the 1-20 ppm range. The formation of G4 in liver tissue was about three times more effective for mouse than rat in this exposure range. Average levels of adduct G4 measured in liver DNA of rats and mice exposed to 5 x 6 h 1, 5 and 20 ppm 1,3-[2,3-(14)C]-butadiene were, respectively, for rats: 0.79 +/- 0.30, 2.90 +/- 1.19, 16.35 +/- 4.8 adducts/10(8) nucleotides and for mice: 2.23 +/- 0.71, 12.24 +/- 2.15, 48.63 +/- 12.61 adducts/10(8) nucleotides. For lung DNA the corresponding values were for rats: 1.02 +/- 0.44, 3.12 +/- 1.06, 17.02 +/- 4.07 adducts/10(8) nucleotides, and for mice: 3.28 +/- 0.32, 14.04 +/- 1.55, 42.47 +/- 13.12 adducts/10(8) nucleotides. Limited comparative data showed that the levels of adduct G4 formed in liver and lung DNA of mice exposed to a single exposure to butadiene in the present 20 ppm study and earlier 200 ppm study were approximately directly proportional across dose, but this was not observed in the case of rats. From the available evidence it is most likely that adduct G4 was formed from a specific isomer of the diol-epoxide metabolite, 3,4-epoxy-1,2-butanediol rather than the diepoxide, 1,2,3,4-diepoxybutane. Another adduct G3, possibly a diastereomer of N7-(2,3,4-trihydroxybutyl)-guanine or most likely the regioisomer N7-(1-hydroxymethyl-2,3-dihydroxypropyl)-guanine, was also detected in DNA of mouse tissues but was essentially absent in DNA from rat tissue. Qualitatively similar profiles of adducts were observed following exposures to butadiene in the present 20 ppm study and the previous 200 ppm study. Overall the DNA adduct levels measured in tissues of both rats and mice were very low. The differences in the profiles and quantity of adducts seen between mice and rats were considered insufficient to explain the large difference in carcinogenic potency of butadiene to mice compared with rats.     

Metabolism of 1,3-butadiene to toxicologically relevant metabolites in single-exposed mice and rats

1,3-Butadiene (BD) was carcinogenic in rodents. This effect is related to reactive metabolites such as 1,2-epoxy-3-butene (EB) and especially 1,2:3,4-diepoxybutane (DEB). A third mutagenic epoxide, 3,4-epoxy-1,2-butanediol (EBD), can be formed from DEB and from 3-butene-1,2-diol (B-diol), the hydrolysis product of EB. In BD exposed rodents, only blood concentrations of EB and DEB have been published. Direct determinations of EBD and B-diol in blood are missing. In order to investigate the BD-dependent blood burden by all of these metabolites, we exposed male B6C3F1 mice and male Sprague-Dawley rats in closed chambers over 6-8h to constant atmospheric BD concentrations. BD and exhaled EB were measured in chamber atmospheres during the BD exposures. EB blood concentrations were obtained as the product of the atmospheric EB concentration at steady state with the EB blood-to-air partition coefficient. B-diol, EBD, and DEB were determined in blood collected immediately at the end of BD exposures up to 1200 ppm (B-diol, EBD) and 1280 ppm (DEB). Analysis of BD was done by GC/FID, of EB, DEB, and B-diol by GC/MS, and of EBD by LC/MS/MS. EB blood concentrations increased with BD concentrations amounting to 2.6 micromol/l (rat) and 23.5 micromol/l (mouse) at 2000 ppm BD and to 4.6 micromol/l in rats exposed to 10000 ppm BD. DEB (detection limit 0.01 micromol/l) was found only in blood of mice rising to 3.2 micromol/l at 1280 ppm BD. B-diol and EBD were quantitatively predominant in both species. B-diol increased in both species with the BD exposure concentration reaching 60 micromol/l at 1200 ppm BD. EBD reached maximum concentrations of 9.5 micromol/l at 150 ppm BD (rat) and of 42 micromol/l at 300 ppm BD (mouse). At higher BD concentrations EBD blood concentrations decreased again. This picture probably results from a competitive inhibition of the EBD producing CYP450 by BD, which occurs in both species.     

Mutagenicity of 1,3-butadiene at the Hprt locus of T-lymphocytes following inhalation exposures of female mice and rats.

The species specific response to 1,3-butadiene (BD), an important industrial chemical, was investigated by determining the influence of exposure duration and exposure concentration on the mutagenicity of BD in mice and rats and by defining the spectra of mutations in the Hprt gene T-cell mutants from control and BD-exposed mice. Female B6C3F1 mice and F344 rats (4-5 weeks old) were exposed by inhalation to 0, 20, 62.5, or 625 ppm of BD for up to 4 weeks (6 h/day, 5 days/week). Groups of control and exposed animals (n=4-12/group) were necropsied at multiple time points after exposure and the T-cell cloning assay was used to measure Hprt mutant frequencies in lymphocytes isolated from spleen. Mutant clones collected from control and BD-exposed mice were propagated and analyzed by RT-PCR to produce Hprt cDNA for sequencing. In animals necropsied 4 weeks after 2 or 4 weeks of BD exposure (0 or 625 ppm), the rate of accumulation of mutations was greater in mice than in rats. Supra-linear dose-response curves were observed in BD-exposed mice, indicating a higher efficiency of mutant induction at lower concentrations of BD. The mutagenic potency estimates (represented by the differences in the areas under the mutant T-cell 'manifestation' curves of treated vs. control animals) in mice were 11 and 61 following 4 weeks of exposures to 62.5 and 625 ppm of BD, respectively, while mutant frequencies (Mfs) in rats were significantly increased only at 625 ppm BD (mutagenic potency of 7). Molecular analysis of Hprt cDNA from expanded T-cell clones from control and BD-exposed mice demonstrated an increased frequency of mutants in exposed animals that likely contain large deletions in the Hprt gene (P=0.016). These data indicate that both exposure duration and exposure concentration are important in determining the magnitude of mutagenic response to BD, and that mutagenic and carcinogenic properties of BD in mice may be related more to the ability of its metabolites to cause chromosomal deletions than to produce point mutations.     

Dose responses for the formation of hemoglobin adducts and urinary metabolites in rats and mice exposed by inhalation to low concentrations of 1,3-[2,3-(14)C]-butadiene

Blood and urine were obtained from male Sprague-Dawley rats and B6C3F1 mice exposed to either a single 6 h or multiple daily (5 x 6 h) nose-only doses of 1,3-[2,3- (14)C]-butadiene at atmospheric concentrations of 1, 5 or 20 ppM. Globin was isolated from erythrocytes of exposed animals and analyzed for total radioactivity and also for N-(1,2,3-trihydroxybut-4-yl)-valine adducts. The modified Edman degradation procedure coupled with GC-MS was used for the adduct analysis. Linear relationships were observed between the exposures to 1,3-[2,3-(14)C]-butadiene and the total radioactivity measured in globin and the level of trihydroxybutyl valine adducts in globin. A greater level of radioactivity (ca. 1.3-fold) was found in rat globin compared with mouse globin. When analyzed for specific amino acid adducts, higher levels of trihydroxybutyl valine adducts were found in mouse globin compared with rat globin. Average levels of trihydroxybutyl valine adduct measured in globin from rats and mice exposed for 5 x 6 h at 1, 5 and 20 ppM 1,3-[2,3-(14)C]-butadiene were, respectively, for rats: 80, 179, 512 pM/g globin and for mice: 143, 351, 1100 pM/g globin. The profiles of urinary metabolites for rats and mice exposed at the different concentrations of butadiene were obtained by reverse phase HPLC analysis on urine collected 24 h after the start of exposure and were compared with results of a previous similar study carried out for 6 h at 200 ppM butadiene. Whilst there were qualitative and quantitative differences between the profiles for rats and mice, the major metabolites detected in both cases were those representing products of epoxide hydrolase mediated hydrolysis and glutathione (GSH) conjugation of the metabolically formed 1,2-epoxy-3-butene. These were 4-(N-acetyl-l-cysteine-S-yl)-1,2-dihydroxy butane and (R)-2-(N-acetyl-l-cystein-S-yl)-1-hydroxybut-3-ene, 1-(N-acetyl-l-cystein-S-yl)-2-(S)-hydroxybut-3-ene, 1-(N-acetyl-l-cystein-S-yl)-2-(R)-hydroxybut-3-ene, (S)-2-(N-acetyl-l-cystein-S-yl)-1-hydroxybut-3-ene, respectively. The former pathway showed a greater predominance in the rat. The profiles of metabolites were similar at exposure concentration in the range 1-20 ppM. There were however some subtle differences compared with results of exposure to the higher 200 ppM concentrations. Overall the results provide the basis for cross species comparison of low exposures in the range of occupational exposures, with the wealth of data available from high exposure studies.     

DNA adducts, strand breaks and micronuclei in mice exposed to styrene by inhalation

Genotoxic and clastogenic effects of styrene were studied in mice. Male NMRI mice were exposed by inhalation to styrene in concentrations of 750 and 1500 mg/m3 for 21, 7, 3 and 1 days (6 h/day, 7 days/week). Followed parameters included styrene in blood, specific styrene oxide (SO) induced DNA adducts, DNA strand breaks and micronuclei. The formation of SO induced 7-SO-guanines and 1-SO-adenines in DNA was analysed from lung tissues by two versions of the 32P-postlabeling technique. In lungs after 21 days of exposure to 1500 mg/m3 the level of 7-SO-guanine was 23.0+/-11.9 adducts/10(8) normal nucleotides, while 1-SO-adenine was detected at the levels of 0.6+/-0.2 adducts/10(8) normal nucleotides. Both 7-SO-guanines and 1-SO-adenines strongly correlated with exposure parameters, particularly with styrene concentration in blood (r=0.875, P=0.0002 and r=0.793, P=0.002, respectively). DNA breaks were measured in peripheral lymphocytes, bone marrow cells and liver cells using comet assay. To discern oxidative damage and abasic sites, endonuclease III was used. In bone marrow of exposed mice slight increase of strand breaks can be detected after 7 days of inhalation. A significant increase was revealed in the endonuclease III-sensitive sites after 21 days of inhalation in bone marrow. In the liver cells inhalation exposure to both concentrations of styrene did not virtually affect either levels of DNA single-strand breaks or endonuclease III-sensitive sites. The inhalation of 1500 mg/m3 of styrene induced significant increase of micronuclei after 7 days of exposure (10.4+/-2.5/1000 cells, i.e. twice higher micronuclei frequency than in controls). After 21 days of inhalation no significant difference between the control group and the two exposed groups was observed. Whether the decrease of micronuclei after 21 days of inhalation was due to the inhibition of cell proliferation caused by styrene or due to the natural elimination of chromatide fragments, remains to be clarified. An interesting link has been found between DNA single-strand breaks in bone marrow and frequencies of micronuclei (r=0.721, P=0.028).     

Cytogenetic studies of mice exposed to styrene by inhalation.

The data for the in vivo genotoxicity of styrene (STY) are equivocal. To evaluate the clastogenicity and sister-chromatid exchange (SCE)-inducing potential of STY in vivo under carefully controlled conditions, B6C3F1 female mice were exposed by inhalation for 6 h/day for 14 consecutive days to either 0, 125, 250 or 500 ppm STY. One day after the final exposure, peripheral blood, spleen, and lungs were removed and cells were cultured for the analysis of micronucleus (MN) induction using the cytochalasin B-block method, chromosome breakage, and SCE induction. Peripheral blood smears were also made for scoring MN in erythrocytes. There was a significant concentration-related elevation of SCE frequency in lymphocytes from the spleen and the peripheral blood as well as in cells from the lung. However, no statistically significant concentration-related increases were found in the frequency of chromosome aberrations in the cultured splenocytes or lung cells, and no significant increases in MN frequencies were observed in binucleated splenocytes or normochromatic erythrocytes in peripheral blood smears.     

Comparison of the mutations at Hprt exon 3 of T-lymphocytes from B6C3F1 mice and F344 rats exposed by inhalation to 1,3-butadiene or the racemic mixture of 1,2:3,4-diepoxybutane

Experiments were conducted to define the spectra of mutations occurring in Hprt exon 3 of T-cells isolated from spleens of female B6C3F1 mice and F344 rats exposed by inhalation to 1,3-butadiene (BD) or its reactive metabolite, (+/-)-diepoxybutane (DEB). Hprt mutant frequencies (Mfs) in BD-exposed (1250 ppm for 2 weeks or 625 ppm for 4 weeks; 6 h/day, 5 days/week) and DEB-exposed (2 or 4 ppm for 4 weeks or 5 ppm for 6 weeks; 6 h/day, 5 days/week) mice and rats were significantly increased over concurrent control values. Mutant T-cell colonies from control and treated animals were screened for mutations in Hprt exon 3 using PCR amplification of genomic DNA and denaturing gradient gel electrophoresis, followed by sequence analysis. Exon 3 mutations were found at the following frequencies: 20/394 (5%) in control mice, 56/712 (8%) in BD-exposed mice, 59/1178 (5%) in BD-exposed rats, 66/642 (10%) in DEB-exposed mice, and 51/732 (7%) in DEB-exposed rats. Mutations in exposed animals included base substitutions, small deletions (1 to 74 bp), and small insertions (1 to 8 bp), with base substitutions predominating. Among the types of base substitutions observed in mice, the proportions of G.C-->A.T transitions (p=0.035, Fisher's Exact Test) and G.C-->C.G transversions (p=0.05) were significantly different in control vs. BD-exposed animals. Given the small number of exon 3 mutants analyzed, there was a high degree of overlap in the mutational spectra between BD-exposed mice and rats, between BD- and DEB-exposed mice, and between BD- and DEB-exposed rats in terms of the sites with base substitutions, the mutations found at those mutated sites, the relative occurrence of the most frequently observed base substitutions, and the occurrence of a consistent strand bias for the most frequently observed base substitutions. The spectra data suggest that adduction of both G.C and A.T bps is important in the induction of in vivo mutations by BD metabolites in exposed mice and rats.     

Metabolic distribution of radioactivity in Sprague-Dawley rats and B6C3F1 mice exposed to 1,3-[2,3-14C]-butadiene by whole body exposure

The uptake of 1,3-[2,3-(14)C]-butadiene and its disposition, measured as radioactivity in urine, faeces, exhaled volatiles and CO(2) during and following 6 h whole body exposure to 20 ppm butadiene has been investigated in male Sprague-Dawley rats and B6C3F1 mice. Whilst there were similarities between the two species, the uptake and metabolic distribution of butadiene were somewhat different for rats and mice. The major differences observed were in the urinary excretion of radioactivity and in the exhalation of 14C-CO(2). After 42 h from the start of exposure, 51.1% of radioactivity was eliminated in rat urine compared with 39.5% for mouse urine. 34.9% of the recovered radioactivity was exhaled by rats as 14C-CO(2), compared with 48.7% by mice. Excretion of radioactivity in faeces was similar for both species (3.8% for rats and 3.4% for mice). The tissue concentrations of 14C-butadiene equivalents measured in liver, testes, lung and blood of exposed mice were 0.493, 0460, 0.457, and 1.626 nmol/g tissue, respectively. The values for the corresponding rat tissues were 0.869, 0.329, 0.457, and 1.626 nmol butadiene equivalents/g tissue, respectively. For rats, 6.2% of recovered radioactivity (0.288 nmol butadiene equivalents/g tissue) was retained in carcasses whereas for mice the amount was 3.6% (0.334 nmol butadiene equivalents/g tissue). There were also some significant differences between the metabolic conversion of 1,3-[2,3-(14)C]-butadiene and excretion by mice following the 20 ppm whole body exposure compared to previously reported data for nose-only exposure to 200 ppm butadiene [Richardson et al., Toxicol. Sci. 49 (1999) 186]. The main difference between the high- and low-exposure studies was in the exhalation of 14C-CO(2). At the 200 ppm exposure, 40% of the radioactivity was exhaled as 14C-CO(2) by rats whereas 6% was measured by this route for mice. The proportional conversion of butadiene to CO(2) by mice was significantly greater at the low exposure concentration compared with that reported for the higher concentration. This shift was not observed for rats. The difference between species could be caused by a saturation of metabolism in mice between 20 and 200 ppm for the pathways leading to CO(2). Restraint or error in collection of CO(2) in the 200 ppm study could also be factors.     

Biological half-time in rats exposed to nickel monosulfide (amorphous) aerosol by inhalation

This study reports the biological half-time of amorphous nickel monosulfide(NiS(A)) aerosol retained in rat lungs. Wistar male rats were exposed to NiS(A) aerosols (mass median aerodynamic diameter: 4.0 μm) for a single 4 h exposure, or for 7 h/d, 5 d/wk for 1 mo. The average exposure concentrations were controlled at 107 mg/m³ for the single exposure and at 8.8 mg/m³ for the repeated exposures by a dust generator consisting of a continuous fluidized bed with an overflow pipe and a screw feeder. After the exposures, the nickel contents in the rat organs, blood, and urine were measured and histopathological examinations were performed. The biological half time of NiS(A) in rat lungs was 20 h, which was extremely shorter than 21 mo of green nickel oxide (NiO(G)). There were no malignant tumors in any of the exposure groups.     

Comparative deposition and clearance of various nickel compounds exposed by inhalation in rats

Wistar male rats were exposed to three types of nickel compounds, NiO(G), NiO(B), and Ni₃S₂, for 6 h/d, 5 d/wk for 6 mo. The solubility of these chemicals to saline solution was 0.3 ppm for NiO(G), 3.5 ppm for NiO(B), and 310 ppm for Ni₃S₂. Controls were exposed to clean air under similar conditions. Some rats were sacrificed 24 h after the termination of the final repeated exposure, and the remaining rats were kept for a 12-mo clearance period before sacrifice. There was no significant difference in body weight between exposed rats and controls and also no significant differences in organs weights, except for lungs in the case of Ni₃S₂, between exposed rats and controls. Nickel concentration in the lungs just after the exposure to nickel compounds was the highest when compared to other organs. The apparent deposition fractions (%) in the lungs were 0.5 ± 0.1 for NiO(G), 1.0 ± 0.3 for NiO(B), and 0.5 ± 0.1 for Ni₃S₂., After the clearance period, there were no significant differences in organ weights, except for the lungs in case of Ni₃S₂, between the exposed rats and the controls. During the 12 mo of clearance, 82% of deposited NiO(G), 73% of NiO(B), and 98% of Ni₃S₂ were cleared from lungs.     

Zinc, copper and iron concentrations in cerebral cortex of male rats exposed to formaldehyde inhalation

Retrospective cohort studies and clinical findings have suggested effects of formaldehyde exposure on the central nervous system in anatomists, embalmers and pathologists. On the other hand, harmful effects of formaldehyde inhalation on the nervous system are not well documented. The concentrations of elements such as zinc, copper and iron within the cerebral cortex indicate whether physiological conditions are maintained. In this study, adult male albino Wistar rats were exposed to formaldehyde at different concentrations (0; 6.1; 12.2 mg x m(-3)) and during different periods of time (subacute-subchronic), and body weights were recorded weekly. Zinc, copper and iron concentrations were measured in the parietal cortex using atomic absorption spectrometry after wet ashing. We conclude that subacute or subchronic exposure to formaldehyde may cause growth retardation and alter zinc, copper and iron levels in the cerebral cortex.     

Evaluation of genetic alterations in cancer-related genes in lung and brain tumors from B6C3F1 mice exposed to 1,3-butadiene or chloroprene

1,3-Butadiene and chloroprene are multisite carcinogens in B6C3F1 mice with the strongest tumor response being the induction of lung neoplasms in females. Incidence of brain tumors in mice exposed to 1,3-butadiene was equivocal. This article reviews the efforts of our laboratory and others to uncover the mechanisms of butadiene and chloroprene induced lung and brain tumor responses in the B6C3F1 mouse. The formation of lung tumors by these chemicals involved mutations in the K-ras cancer gene and loss of heterozygosity in the region of K-ras on distal chromosome 6, while alterations in p53 and p16 were implicated in brain tumorigenesis.     

Urinary excretion of mandelic, phenylglyoxylic, and specific mercapturic acids in rats exposed repeatedly by inhalation to various concentrations of styrene vapors

Adult male Sprague-Dawley rats were exposed by inhalation to various concentrations of styrene vapors (25, 50, 100, or 200 ppm) 6 h/day, 5 days/week, for 4 consecutive weeks. The concentrations were varied from day to day according to a random pattern allowing treated animals to be exposed five times to each concentration of styrene. Each day, the following urinary metabolites were analysed from samples collected during exposure (0-6 h) and after exposure (6-24 h): mandelic acid; phenylglyoxylic acid; and two mercapturic acids, N-acetyl-S-(1-phenyl-2-hydroxyethyl)-L-cysteine (M1) and N-acetyl-S-(2-phenyl-2-hydroxyethyl)-L-cysteine (M2). Various parameters of renal toxicity and hepatic microsomal and cytosolic enzyme activities were also measured. The results show that there is a very good relationship between the excretion of all four styrene metabolites and the degree of daily exposure to styrene over the entire period of urine collection, with correlation coefficients ranging from 0.82 to 0.98. The correlation was poor for mandelic acid during the 0-6 h period. There was no evidence that repeated exposure to styrene caused renal toxicity, nor induced hepatic microsomal enzyme activities; cytosolic glutathione S-transferase activity was increased moderately by 1.5 times. Thus, under conditions of exposure to styrene likely to be found in the workplace, all four metabolites measured were good indicators of styrene exposure throughout the length of the experiment. Since mercapturic acids result from the conjugation of styrene oxide with glutathione, the data suggest that measurement of these metabolites offers the possibility to monitor internal exposure to a toxic electrophilic compound more directly.     

DNA damage induced by three major metabolites of 1,3-butadiene in human hepatocyte L02 cells

1,3-Butadiene (BD) is a carcinogenic air pollutant. Its bioactivation produces four major metabolites, i.e., 3,4-epoxy-1-butene (EB), 3,4-epoxy-1,2-butanediol (EBD), 1,2,3,4-diepoxybutane (DEB), and 3-butene-1,2-diol (BDD). Studies have been mostly focused on DEB due to its strong mutagenicity/carcinogenicity. In contrast, studies of genotoxicity of EB, EBD, and BDD have been limited. In particular, genotoxicity of EBD and BDD using strand breaks as the endpoint has not been investigated. To obtain a more complete understanding of BD toxicity, in the present study, we used comet assay to investigate DNA damage induced by EB, EBD, and BDD in human hepatocyte L02 cells, with the aim to determine their relative potencies, the types of DNA damage, and the possible pathway to form strand breaks. Using alkaline comet assay (pH>13), it was observed that EB and EBD caused similar concentration-dependent increases in DNA migration from 50 to 1000μM. However, BDD induced a statistically significant increase only at 1000μM, and the increase itself was very small. EBD was as potent as EB at lower concentrations (≤200μM), and was slightly less potent than EB at higher concentrations. The results indicated that these metabolites could generate strand breaks in cells with the rank order of the potencies being EB>≈EBD?BDD. All three compounds failed to cause statistically significant increases in DNA migration in pre-lysed cells, suggesting that they did not produce strand breaks through chemical pathways under our experimental conditions. By using comet assays at pH 11.9 and pH 9, it was demonstrated that EB and EBD generated both single-strand breaks (SSB) and alkali-labile sites, but BDD produced only SSB. To our knowledge, this is the first report to investigate EBD- and BDD-induced strand breaks in cells. The results implied that EBD could play an important role in toxicity of BD.     

The association between genetic damage in peripheral blood lymphocytes and polymorphisms of three glutathione S-transferases in Chinese workers exposed to 1,3-butadiene

1,3-Butadiene (BD) has been classified as a human carcinogen, group I; however, the relationship between polymorphisms of glutathione S-transferases that metabolize BD and chromosomal damage is not clear. The present study used sister chromatid exchange (SCE) and cytokinesis-block micronucleus (CBMN) assays to detect chromosomal damage in peripheral lymphocytes of 44 BD-exposed workers and 39 non-exposed healthy controls. PCR and PCR-RFLP were employed to detect three known glutathione S-transferase polymorphisms GSTT1, GSTM1, and GSTP1 (Ile105Val). The data demonstrated that the micronucleus (CBMN) frequency in BD-exposed workers was significantly higher than that in controls (frequency ratio (FR) = 1.48, 95% CI: 1.14–1.91, P < 0.01), and the CBMN frequency was higher in workers exposed to higher cumulative BD levels (FR = 1.70, 95% CI: 1.28–2.27, P < 0.01). However, differences in SCE frequency were not observed (FR = 1.14, 95% CI: 0.81–1.61, P > 0.05). Among exposed workers, chromosomal damage was related to BD exposure levels (FR = 1.35, 95% CI: 1.02–1.80, P < 0.05); age, older workers exhibited higher MN frequencies than younger workers (FR = 1.45, 95% CI: 1.14–1.84, P < 0.05); and years of work, those with more years of work exhibited higher MN frequencies than those with fewer years (FR = 1.40, 95% CI: 1.10–1.77, P < 0.05). Multivariate Poisson regression analysis showed that those who carried GSTM1 (?) (FR = 1.48, 95% CI: 1.14–1.92) or GSTT1 (?) (FR = 1.42, 95% CI: 1.10–1.83) genotypes, and especially those who carried both (FR = 2.10, 95% CI: 1.43–3.09) exhibited significantly higher MN frequencies than those carrying GSTM1 (+), GSTT1 (+) genotypes or their combination. The GSTP1 Val genotype did not affect MN frequency (P > 0.05). Our results suggested that higher levels of BD exposure in the workplace resulted in increased chromosomal damage, and that polymorphisms in GSTT1 and GSTM1 genes might modulate the genotoxic effects of BD exposure. Furthermore, the GSTT1 and GSTM1 polymorphisms exhibited an additive effect. Finally, urinary DHBMA was found to provide a biomarker that correlated with airborne BD levels.     

Persistence of 7-(2-hydroxyethyl) guanine-DNA adducts in rats exposed to ethene by inhalation

Quantification of 7 2 hydroxyethyl guanine 7 HEG adduct in DNA of livers and lymphocytes of male Sprague-Dawley rats exposed to 300 ppm ethene by inhalation 12 h a day for three consecutive days was performed to evaluate the potential of ethene to produce DNA adducts in these tissues. The persistence of 7 HEG in livers and lymphocytes was studied in rats sacrificed 0, 1, 5, and 20 days after the last exposure. DNA samples from control and treated animals were analysed for 7 HEG and 7 methylguanine 7 MG adducts by thin layer chromatography TLC combined with a high pressure liquid chromatography HPLC assay. After a 3 day exposure to ethene, 7 HEG accumulated to a similar extent in liver and lymphocytes, with the mean adduct level of 7.0 0.7 adducts per 107 nucleotides in liver and 7.4 0.7 adducts per 107 nucleotides in lymphocytes of rats sacrificed immediately after cessation of exposure. The approximate half life of 7 HEG was 5 days in liver and 3 days in lymphocytes, which is consistent with the loss of adduct primarily by spontaneous depurination. In addition, the background levels of 7 HEG and 7 MG were determined in the liver and lymphocytes from the control rats.     

Exposure and risk assessment of 1,3-butadiene in Japan

1,3-Butadiene is on the list of Substances Requiring Priority Action published by the Central Environmental Council of Japan in 1996. Emission of 1,3-butadiene has been controlled by a voluntary reduction program since 1997. Although the industrial emission of 1,3-butadiene in Japan has decreased in recent years, primarily due to a voluntary industrial emissions reduction program, the risks of exposure to it remain largely unknown. We assessed the risks and consequences of exposure to 1,3-butadiene on human health. A remarkable advantage of our risk assessment approach is the detailed assessment of exposure. Previously, we developed two different models that can be applied for the assessment of exposure: the first, the AIST-ADMER model estimates regional concentration distributions, whereas the second, the METI-LIS model estimates concentration distributions in the vicinity of factories. Both models were used for the assessment of exposure to 1,3-butadiene. Using exposure concentration and carcinogenic potency determined and reported by Environment Canada and Health Canada, we evaluated the excess lifetime cancer risk for persons exposed to 1,3-butadiene over the course of a lifetime. The results suggested that the majority of the population in Japan has an excess lifetime cancer risk of less than 10(-5), whereas a small number of people living close to industrial sources had a risk of greater than 10(-5). The results of the present assessment also showed that 1,3-butadiene in the general environment originates primarily from automobile emissions, such that a countermeasure of reducing emissions from cars is expected to be effective at reducing the total cancer risk among Japanese. On the other hand, individual risks among a population living in the vicinity of certain industrial sources were found to be significantly higher than those of the population living elsewhere, such that a reduction in emissions from a small number of specific industrial sources should be realized in order to reduce the high level of individual risk. Based on the results of our assessment, the Industrial Structure Council of the Ministry of Economy, Trade and Industry (METI) in Japan decided to announce that the voluntary reduction program had been successful, and that emissions reductions should no longer be targeted across all industries in general, but instead that such reductions should be carried out in a small number of selected factories that emit excessively large amounts of emissions.