Examination of ras oncoproteins in human plasma from healthy controls and workers exposed to petroleum emissions, including benzene-related compounds.

Ras oncoproteins in blood plasma from workers exposed to petroleum emissions and unexposed controls were examined from Polish and Estonian samples. Twenty-four workers and 35 unexposed controls were examined from Poland and 97 exposed and 40 unexposed controls from Estonia. Of the Estonian workers, 50 were exposed to benzene in a benzene production plant and 47 to polyaromatic hydrocarbons and benzene in a cokery. Blood plasma proteins were separated by gel electrophoresis, transferred to a nitrocellulose membrane by Western blotting and detected by chemiluminescence using a monoclonal antibody as the primary antibody. There were no statistically significant differences between the exposed and the control groups in either the Polish or the Estonian samples.

Low response in white blood cell DNA adducts among workers in a highly polluted cokery environment.

Coke oven workers are often heavily exposed to polynuclear aromatic hydrocarbons (PAHs); this exposure has been associated with higher cancer rates among these workers. We assessed the exposure of cokery workers in an oil shale processing plant. Personal hygienic monitoring, measurement of urinary 1-hydroxypyrene (1-OHP), and analysis of PAH-DNA adducts in white blood cells (WBCs) were performed. The 32P-postlabeling method was used for adduct measurement. The mean adduct value, 1.6 adducts per 10(8) nucleotides, did not differ significantly from the control value (P = 0.098). Smokers had significantly higher adduct levels than non-smoking workers (P = 0.002). 1-OHP levels measured in post-shift samples correlated with DNA adducts found in white blood cells (WBCs). We conclude that hygienic monitoring and measurement of urinary metabolites are essential background exposure data when the biologically effective dose of chemical carcinogens is assessed.

GSTT1-dependent induction of centromere-negative and -positive micronuclei by 1,2:3,4-diepoxybutane in cultured human lymphocytes.

The role of the glutathione S-transferase T1 gene (GSTT1) in determining genotoxic response to 1,2:3,4-diepoxybutane (DEB), an epoxide metabolite of 1,3-butadiene, was studied by analysis of micronuclei (MN) in cultured human lymphocytes using the cytokinesis block method. Fluorescence in situ hybridization (FISH) with an alphoid satellite DNA probe specific for the centromeres of all human chromosomes was applied to identify MN harboring whole chromosomes. Whole-blood lymphocyte cultures of 11 GSTM1 (glutathione S-transferase M1)-positive individuals (i.e. having at least one GSTM1 allele), of whom six were GSTT1-positive (with at least one GSTT1 allele) and five GSTT1-null (GSTT1 homozygously deleted), were treated for 48 h (starting 24 h after culture initiation) with two different concentrations (2 and 5 muM) [corrected] of DEB. The GSTT1-null individuals were excessively sensitive to DEB, showing, on average, approximately 2.5 times higher induced MN frequency (control frequency subtracted) than the GSTT1-positive donors, both at 2 muM [corrected] (mean/1000 binucleate cells 29.8 versus 11.8, P < 0.05) and 5 muM [corrected] (87.6 versus 34.0, P < 0.001) DEB. In accordance with the known strong clastogenicity of DEB, MN without centromeric FISH signals were particularly increased, the difference between the two GSTT1 genotypes being statistically significant at both concentrations of DEB (mean induced MN/1000 binucleate cells 23.1 versus 9.9, P < 0.05, at 2 muM [corrected]; 69.7 versus 24.2, P < 0.001, at 5 muM) [corrected]. In addition, centromere-positive (C+) MN were induced, suggesting that DEB also has some aneuploidogenic activity. The GSTT1-null genotype showed a significantly (P < 0.05) higher mean frequency of induced C+ MN than the GSTT1-positive genotype, at both 2 (6.7 versus 1.9) and 5 muM [corrected] (17.9 versus 9.8) DEB. At the higher dose mean nuclear division index was lower in the GSTT1-null group (1.80) than in the GSTT1-positive group (2.05, P < 0.01). These findings support earlier results from the analysis of sister chromatid exchange showing that individual sensitivity to the genotoxic and cytotoxic effects of DEB is largely explained by lack of the GSTT1 gene.

Biological monitoring of exposure to benzene in the production of benzene and in a cokery.

The purpose of this study was to compare different biological methods in current use to assess benzene exposure. The methods involved in the study were: benzene in blood, urine and exhaled air, and the urinary metabolites t,t-muconic acid (MA) and S-phenylmercapturic acid (S-PMA). Blood, urine and exhaled air samples were collected from workers in a benzene plant (pure benzene exposure) and cokery (mixed exposure, e.g. polycyclic aromatic hydrocarbons--PAHs) in an Estonian shale oil petrochemical plant. The benzene in these samples was analysed with a head-space gas chromatograph, and the metabolites MA and S-PMA with a liquid chromatograph using methods developed from published procedures. Some of the values measured in the Estonian shale oil area were high in comparison with those published during the last few years, whereas the values measured in the control group did not show any exposure to benzene except in the smokers group. The highest median exposure was in the benzene factory, 0.9 cm3/m3 TWA (2.9 mg/m3) and the highest individual value was 15 cm3/m3 TWA (49 mg/m3). All biological measurements in this study gave the same assessment about exposure to benzene and correlated highly significantly with each other and with the air measurements (r = 0.8 or more). In the benzene factory the correlation was good even when calculated from samples with air concentration < 1 cm3/m3 (3.2 mg/m3) in the case of blood benzene and urinary MA. However, for S-PMA it was weak (r = 0.4) and for benzene in urine and exhaled air it did not exist any more. In the cokery, with mixed exposure, the correlation at low levels was weaker even for blood benzene and urinary MA (r = 0.6). According to the results in the benzene factory the exposure to pure benzene at the level 1 cm3/m3 (3.25 mg/m3) TWA gave: the blood benzene value about 110 nmol/l (8.6 micrograms/l), MA 23 mumol/l (3.3 micrograms/l) or 2.0 mg/g creatinine, S-PMA 58 micrograms/g creatinine or 0.4 mumol/l (95.7 micrograms/l), benzene in urine 499 nmol/l (39 micrograms/l), and benzene in the exhaled air 2.8 nmol/l (0.2 microgram/l). In general, the measurement of benzene in blood and in exhaled air, as well as benzene and its metabolites MA and S-PMA in urine, all gave similar results. However, at low exposure level (< 1 cm3/m3) the most reliable analyses were MA in urine and benzene in blood.

Molecular cytogenetic analysis of buccal cells and lymphocytes from benzene-exposed workers.

Benzene is a well-characterized human carcinogen and clastogen still present in both the occupational and general environment. However, the levels of benzene encountered today are, in most cases, relatively low and new methods, more specific and sensitive than classical cytogenetics, are probably needed to assess if current benzene exposures pose a genotoxic risk to human health. Bearing in mind the leukaemogenic action of benzene, blood lymphocytes appear to be a suitable cell system for biomonitoring studies. Buccal epithelium is an alternative source of tissue for monitoring human exposure to inhaled occupational and environmental genotoxicants. New molecular cytogenetic techniques allowing us to specifically study clastogenic or aneugenic events in human cells may provide the additional sensitivity required. In the present study, fluorescence in situ hybridization was used to examine the content of micronuclei (MN) (using the pan-centromeric DNA probe SO-alphaAllCen) in lymphocytes and buccal cells and to detect numerical abnormalities of chromosome 9 (using a chromosome 9 centromere-specific alphoid DNA probe) in buccal cells from a population occupationally exposed to benzene in an Estonian petrochemical plant. Age-matched Estonian volunteers were used as a control group. Individual benzene exposure levels were estimated to be around 1 p.p.m. (8 h time-weighted average). No increases in the frequency of total MN, MN harbouring whole chromosomes or acentric chromosomal fragments or chromosome 9 numerical abnormalities were detected in relation to benzene exposure in the present study. The lack of positive results was consistent in both buccal cells and lymphocytes, indicating that the benzene exposure levels encountered did not induce detectable clastogenic or aneugenic effects in the exposed workers. Other variables and confounding factors, such as age, smoking or alcohol consumption, did not influence any of the multiple cytogenetic biomarkers analysed.

32P-postlabelling/HPLC assay reveals an enantioselective adduct formation in N7 guanine residues in vivo after 1,3-butadiene inhalation exposure.

We have established a protocol that allows qualitative and quantitative determination of butadiene monoepoxide-DNA adducts formed as a result of inhalation exposure to 1,3-butadiene. We observed that in this particular case in vivo samples required extensive sample purification to facilitate a low background. Sample preparation included a solid phase extraction carried out with a strong anion exchange column and one-dimensional ion exchange TLC. The ultimate analysis is based on reverse phase HPLC with on-line radioactivity and UV detectors. The qualitative identification and quantitation is based on characterized markers, which are used as external and internal standards. Modified 3'-dGMP markers were used to control labelling efficiency, which varies, and modified 5'-dGMP markers were used as an optical standard to qualitatively assign the products and to determine recovery of the sample preparation. Using this method we were able to demonstrate, for the first time, specific enantio- and regioisomeric adduct formation at the N7 position of guanine residues in liver DNA of rats inhalation-exposed to 1,3-butadiene. The major adduct formed was the C-2 isomer derived from the R enantiomer of butadiene monoepoxide, contributing 47% of all adducts formed at the N7 position of guanine. The relative proportions of the remaining three other adducts detected were 22 (R C-1), 18 (S C-2) and 14% (S C-1) respectively. Inhalation exposure to 200 p.p.m. for 5 days resulted in an alkylation level of 7.2 fmol/10 microg DNA or 2.4 adducts/10(-7) normal nucleotides.

Assessment of occupational exposure to PAHs in an Estonian coke oven plant- correlation of total external exposure to internal dose measured as 1-hydroxypyrene concentration.

The exposure of cokery workers to polynuclear aromatic hydrocarbons at an Estonian oil shale processing plant was assessed by using occupational hygiene and biomonitoring measurements which were carried out twice, in midwinter and in the autumn. To assess the external dose of polynuclear aromatic hydrocarbons, pyrene and benzo[a]pyrene concentrations were measured from the breathing zone of workers during a workshift. Skin contamination with pyrene and benzo[a]pyrene was assessed by skin wipe sampling before and after the workshift. As a biomarker of overall exposure to polynuclear aromatic hydrocarbons, and as an integral of all absorption routes of pyrene, 1-hydroxypyrene concentration was measured from post shift urine samples. Of the personal air samples, 18% exceeded the Finnish threshold limit value of benzo[a]pyrene (10 µg m(-3)). Mean value (two separate measurements together) for benzo[a]pyrene was 5.7 µg m(-3) and for pyrene, 8.1 µg m(-3). Based on skin wipe sample analyses, the skin contamination was also obvious. The mean value of benzo[a]pyrene in the samples collected after the shift was 1.2 ng cm(-2). Benzo[a]pyrene was not found in control samples. The mean value of urinary 1-hydroxypyrene concentration was 6.0 µmol mol(-1) creatinine for the exposed workers and 0.5 µmol mol(-1) creatinine for the controls. This study undoubtedly shows the usefulness of 1-hydroxypyrene as an indicator of internal dose of polynuclear aromatic hydrocarbons. It can be concluded that the cokery workers at the Kohtla-Järve plant are exposed to high concentrations of polynuclear aromatic compounds, and the exposure level is considerably higher during the winter measurements.

Examination of ras (P21) proteins in plasma from workers exposed to benzene emissions from petrochemical plants and healthy controls.

Exposure of workers to benzene and polyaromatic hydrocarbons has been documented to be at relatively high levels in the production of benzene and in the coking process at a petrochemical plant in the oil shale area in Estonia. Altogether 97 plasma samples from workers and 40 from unexposed matched referents from two samplings in different seasons were analyzed for the presence of ras (P21) proteins; of the workers 50 were exposed to benzene in the benzene production plant and 47 to polyaromatic hydrocarbons and benzene in a cokery. Proteins were separated by gel electrophoresis, transferred to a nitrocellulose membrane by Western blotting and detected by chemiluminescence, using a monoclonal antibody as the primary antibody. There were no statistically significant differences between the exposed and the referent groups. The results are thus in keeping with the lack of exposure related cytogenetic effects for this same workforce.

Induction of sister chromatid exchange by 3,4-expoxybutane-1,2-diol in cultured human lymphocytes of different GSTT1 and GSTM1 genotypes.

The induction of sister chromatid exchanges (SCEs) by a 48-h treatment with 3,4-epoxybutane-1,2-diol (EBD), a metabolite of 1,3-butadiene, was studied in whole-blood lymphocyte cultures of 22 human donors with known genotypes of two polymorphic glutathione S-transferases (GSTs), GSTT1 and GSTM1. For both genes, donors representing a homozygous 'null' genotype lacking the respective GST gene and isozyme and a 'positive' genotype with at least one intact gene and GST activity were included. The mean frequencies of SCE/cell were similar in all genotype groups: GSTT1 null (n = 10) (mean 22.0 for 250 microM and 32.9 for 500 [corrected] microM of EBD), GSTT1 positive (n = 14) (21.3 and 34.6, respectively), GSTM1 null (n = 10) (20.3 and 33.5) and GSTM1 positive donors (n = 15) (20.6 and 34.8). At 500 microM concentration of EBD, the lymphocyte cultures of all donors showed a significantly decreased replication index. No differences in EDB-induced SCEs or in replication index could be associated with the GSTM1 and GSTT1 genotypes either separately or in combination. When SCE induction by EBD was compared to that of two other known epoxide metabolites of butadiene, 1,2:3,4-diepoxybutane (DEB) was effective at concentrations over two orders of magnitude lower than EBD or 1,2-epoxy-3-butene (MEB). It is concluded that EBD is an efficient inducer of SEC in cultured human lymphocytes, although not quite as effective as MEB and clearly less effective than DEB. Contrary to previous findings with DEB and MEB, the polymorphic GSTM1 and GSTT1 do not appear to be involved in the detoxification of EBD in human lymphocytes.

Assessment of exposure to butadiene in the process industry.

Occupational exposure levels to 1,3-butadiene (BD) are variable but generally below 1 ppm in the European process industry. A preliminary analysis showed that hemoglobin adduct levels of butadiene monoxide (BMO) were increased among the worker groups with higher potential exposure to BD (process work, bomb voiding, repair duties) than among less exposed workers in maintenance and laboratory or control persons. In the same workers no exposure related effects were seen in the cytogenetic parameters studied, i.e. chromosomal aberrations, sister chromatid exchanges or micronuclei in peripheral blood lymphocytes. However, the glutathione-S-transferase polymorphism in the T1 gene might play a role in determining interindividual sensitivity to BD-induced chromosomal aberrations. Chromosomal aberrations (gaps excluded) were significantly (P < 0.05) increased among the workers lacking the GSTT1 gene as compared to the BD workers with the gene, while the other polymorphic GSTM1 gene showed no association with the cytogenetic parameters. More work needs to be done to study the adducts by other active BD metabolites than BMO and the role of the genetic polymorphisms controlling the variability of individual responses.

Monitoring of occupational exposure to cytostatic anticancer agents.

Many anticancer agents have been shown to be carcinogenic, mutagenic and teratogenic in experimental animals and in in vitro test systems. Epidemiological data on the association of second neoplasms with a specific chemotherapy treatment is available on some 30 agents, and in the case of 10 compounds the overall evidence on human carcinogenicity has been evaluated to be conclusive (Group 1: IARC, 1987 and 1990). The primary source of human exposure to anticancer drugs is from their use in therapy of cancer. However, persons employed in the manufacture, preparation and administration of the drugs to patients and in nursing patients may also be exposed. Safe handling of anticancer drugs, since the introduction of various general handling guidelines, is now good practice in hospitals, pharmacies and drug manufacturing companies of most developed countries. Careless handling of cancer chemotherapeutic agents may lead to exposure of the personnel in amounts detectable with chemical or biological methods in the body fluids or cell samples of the subjects. The exposure is typically to mixed compounds over long-term and to low exposure levels with accidental peaks. Therefore, the use of biological exposure markers is appropriate for the monitoring of such exposure patterns. The biological markers/methods for exposure assessment are either non-specific (e.g., cytogenetic damage, point mutations or 32P-post-labelling adducts in peripheral blood lymphocytes, urinary mutagenicity) or specific for a given compound (immunological methods for DNA adducts, specific analytical methods). Studies have revealed minor amounts of cyclophosphamide in the urine of pharmacy technicians and nurses handling the drug even when taking special safety precautions (Sessink et al. (1994a) J. Occup. Med., 36, 79; Sessink et al. (1994b) Arch. Env. Health, 49, 165). Another study showed surface wipe samples with measurable cyclophosphamide even away from the handling site (McDevitt et al. (1993) J. Occup. Med., 5, 57). These studies strongly implicate the importance of skin absorption as an exposure route. Also accidental spillage is never completely avoidable (Sorsa et al. (1988) Mutation Res., 204, 465-479). The potential confounders (smoking etc.), toxicokinetics of the agent(s) to be assessed and individual working practices should be carefully considered in any exposure assessment studies using human body fluid samples. Environmental monitoring on indicator cytostatics should be combined into studies designed to identify potential occupational exposure situations to anticancer agents. A properly performed study should also include dissemination of information to the workers to create a psychologically positive atmosphere for this important work.

Exposure to PAH compounds among cokery workers in the oil shale industry.

The exposure of Estonian cokery workers to polynuclear aromatic hydrocarbons at an oil shale processing plant was assessed by occupational hygiene and biomonitoring measurements. To assess the external dose of exposure to polynuclear aromatic hydrocarbons, pyrene and benzo[a]pyrene concentrations were measured from the breathing zone of workers during a workshift. Skin contamination with pyrene and benzo[a]pyrene was assessed by skin wipe sampling. As a biomarker of exposure to polynuclear aromatic hydrocarbons and as an integral of all possible absorption routes of pyrene, 1-hydroxypyrene concentration was measured from post-shift urine samples. Eighteen percent of the personal air samples exceeded the Finnish threshold limit value of benzol[a]pyrene (10 micrograms/m3). Mean values for benzo[a]pyrene and pyrene were 5.7 micrograms/m3 and 8.1 micrograms/m3, respectively. Based on skin wipe sample analyses, the skin contamination was also obvious. The mean value of benzo[a]pyrene on the samples collected after the shift was 1.2 ng/cm2. In control samples, benzo[a]pyrene was not found. The mean value of urinary 1-hydroxypyrene concentration was 6.0 nmol/mmol creatinine for the exposed workers and 0.5 nmol/mmol creatinine for the controls. This study showed the usefulness of 1-hydroxypyrene as an indicator of internal dose of polynuclear aromatic hydrocarbons. We concluded that the cokery workers at the Kohtla-Järve plant are exposed to high concentrations of polynuclear aromatic compounds.

Inhalation exposure of rats and mice to 1,3-butadiene induces N6-adenine adducts of epoxybutene detected by 32P-postlabeling and HPLC.

In this paper we report DNA binding of butadiene monoepoxide, a first metabolite of 1,3-butadiene catalyzed by monooxygenases. We prepared alkylated purines as marker compounds for 32-P-postlabeling and electrochemical analysis and developed methods to measure the corresponding products. The traditional postlabeling assay was modified by incorporating a solid phase extraction column and high-performance liquid chromatography (HPLC) enrichment steps to the assay prior to labeling. The final analysis of adducted N6 adenines is based on two dimensional thin-layer chromatography (TLC) and an on-line HPLC/radioactivity analysis. The qualitative and quantitative results are based on positively identified marker compounds. Alkylated N7 guanines were released from DNA by neutral thermal hydrolysis, prepurified by HPLC, and analyzed by HPLC with a sensitive electrochemical detection procedure. By using these methods, we found alkylation of calf thymus DNA exposed to butadiene monoepoxide in vitro at adenine N6 and guanine N7 sites. Analysis of lung DNA samples from mice and rats exposed to butadiene through inhalation showed that adenine N6 adducts were formed in vivo in a dose responsive manner.

Ethical aspects of genetic predisposition to environmentally-related disease.

Some individuals are highly susceptible to disease caused by chemical exposures and this hypersusceptibility can be genetically determined. Because biomarker technology for the determination of genetic predisposition is at the disposal of researchers, the capability therefore exists to include genetic screening in epidemiologic studies. The application of this technological advance in population-based research is, however, fraught with ethical tensions heretofore unknown. Moral duties alone are of limited use in resolving these problems. Scientific documentation is almost always insufficient to clarify the exact nature of the ethical implications, and ways to deal with uncertainties arising as a result of information generated from genetic screening studies must be considered. The most important tensions relate to autonomy and the right to privacy, fairness and equality, while balancing potential public interest in paternalistic measures. Because no moral framework has been accepted for dealing with this technological advance, an ethical discourse in an open forum is required with all affected parties. Scientists alone, or any other group in isolation, should not expect to resolve these questions, but they should participate in and facilitate the process.

Haemoglobin adducts as biomarkers of occupational exposure to 1,3-butadiene.

Adducts of 1,2-epoxy-3-butene (EB) with haemoglobin were monitored in 17 workers from the 1,3-butadiene (BD) production unit of a petrochemical plant and in nine referents employed at the same factory but not exposed to BD. The air concentrations of BD were determined using stationary and personal monitoring. The ambient level of exposure of the plant workers handling butadiene containers (sampling and voiding) was on average 11.2 +/- 18.6 (mean +/- SD) mg/m3. Maintenance and laboratory workers were exposed to levels < or = 1.2 mg/m3. The particular haemoglobin adduct measured was 2-hydroxy-3-butenylvaline, formed by reaction of N-terminal valine with carbon 1 in EB. The adduct levels were increased (0.16 +/- 0.099 pmol/g; n = 10) in plant workers compared with the levels in maintenance and laboratory workers and controls (approximately 0.05 pmol/g; seven laboratory workers and nine controls evaluated). Thus, the method used for adduct determination--derivatization of 200-300 mg globin samples with penta-fluorophenyl isothiocyanate according to the N-alkyl Edman method and detection of the thiohydantoin derivatives by tandem mass spectrometry--is sufficiently sensitive to allow monitoring of exposure to BD down to the p.p.m. level.

Levels of ras oncoproteins in human plasma from 1,3-butadiene-exposed workers and controls.

In a Czech plant near Prague, 10 samples from male workers occupationally exposed to 1,3-butadiene and 13 exposed to 1,3-butadiene/styrene were compared with unexposed male negative controls, matched for age and smoking habits, for the presence of ras oncoproteins in their plasma. Proteins were separated by gel electrophoresis, transferred to a nitrocellulose membrane by Western blotting and detected by chemiluminescence, using monoclonal ras antibody as the primary antibody. There were no statistically significant differences between the 3 groups (pooled two-sample t-test, untransformed and non-parametric Mann-Whitney test). These results are in keeping with the lack of exposure-related effects for 3 cytogenetic endpoints (chromosome aberrations, sister chromatid exchanges and micronuclei) already reported (Sorsa et al., 1994 Mutation Res., 309, 321-326) for this work-force exposed to low (below 3 ppm) exposure levels.

Assessment of environmental and occupational exposures to butadiene as a model for risk estimation of petrochemical emissions.

1,3-Butadiene (BD) is an important industrial chemical and environmental contaminant, e.g. in urban air, traffic exhausts and tobacco smoke. It has been shown to be genotoxic in vitro and in vivo and carcinogenic in rodents, mice being more sensitive than rats. The present study confirmed this species difference. Using micronuclei in erythrocytes or bone marrow as a marker, mice responded at an effective level of 50 p.p.m., while the highest ineffective level in rats was 500 p.p.m. (inhalation of BD for 5 days). A dose-dependent increase in N-terminal valine haemoglobin adducts was seen in both rats and mice, but the adduct levels in the latter species were on average five times higher. For the first time, specific N6-alkyldeoxyadenosine adducts were identified in lung and liver DNA of rats exposed to BD by inhalation. No significant difference in DNA adduct level was seen in lung tissue of rats and mice at similar exposure levels. Occupational exposure levels to BD in the European Process industry are variable, but generally < 1 p.p.m. Haemoglobin adduct levels were seen to be increased among the worker groups with higher potential exposure to BD (process work, bomb voiding and repair duties) as compared with adduct levels in less exposed workers in maintenance and the laboratory or control personnel. However, the N-terminal valine haemoglobin adducts measured in the workers were one to two orders of magnitude lower than extrapolated for the same exposure dose in mice. In the same workers no exposure-related effects were seen in the cytogenetic parametres studied, i.e. chromosomal aberrations, sister chromatid exchanges or micronuclei in peripheral blood lymphocytes, or in the Ras oncoprotein levels of plasma samples. The studies so far conducted suggest that human exposure at the levels seen in the present day process industry can be documented at the biological dose level using haemoglobin adduct measurement, but not at the biological effect level using cytogenetic biomarkers. In order to quantitate the human genotoxic risk of BD exposure more work needs to be done on the role of other active BD metabolites than 1,2-epoxy-3-butene and on the genetic polymorphisms controlling the variability of individual responses.

Simultaneous determination of pseudouridine, neopterine and creatinine in urine by ion-pair high-performance liquid chromatography with in-series ultraviolet and fluorescence detection.

A simple, fast and precise method for the simultaneous determination of neopterine (Npt), pseudouridine (Psu) and creatinine (Cre) in urine by using ion-pair HPLC has been developed. The urine specimen is subjected to a microcolumn clean-up step, providing a ten-fold sample dilution, and is then injected into the column. The eluate is forced through the respective cells of a fluorescence and then a UV detector, which are connected in series. Neopterine is monitored by fluorescence emission at 438 nm (excitation wavelength 353 nm) while Psu and Cre are monitored by UV absorption at 235 nm. This allows the determination of Npt/Cre and Psu/Cre concentration ratios in a single run on the same sample, and the use of urine specimens collected randomly instead of 24 hourly collections. The method has been applied to urine specimens from 19 healthy, male donors (mean Npt/Cre (mumol/mol) and Psu/Cre (mumol/mmol) values of 41.7 and 16.8, respectively) and 23 healthy, female donors (mean Npt/Cre (mumol/mol) and Psu/Cre (mumol/mol) values of 67.4 and 18.5, respectively). The within-run S(r) for Npt/Cre and Psu/Cre concentration ratios ranged between 3.3 and 4.6%.

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.