Structure-activity relationships for perfluoroalkane-induced in vitro interference with rat liver mitochondrial respiration.

Perfluorinated alkyl acids (PFAAs) represent a broad class of commercial products designed primarily for the coatings industry. However, detection of residues globally in a variety of species led to the discontinuation of production in the U.S. Although PFAAs cause activation of the PPARα and CAR nuclear receptors, interference with mitochondrial bioenergetics has been implicated as an alternative mechanism of cytotoxicity. Although the mechanisms by which the eight carbon chain PFAAs interfere with mitochondrial bioenergetics are fairly well described, the activities of the more highly substituted or shorter chain PFAAs are far less well characterized. The current investigation was designed to explore structure-activity relationships by which PFAAs interfere with mitochondrial respiration in vitro. Freshly isolated rat liver mitochondria were incubated with one of 16 different PFAAs, including perfluorinated carboxylic, acetic, and sulfonic acids, sulfonamides and sulfamido acetates, and alcohols. The effect on mitochondrial respiration was measured at five concentrations and dose-response curves were generated to describe the effects on state 3 and 4 respiration and respiratory control. With the exception of PFOS, all PFAAs at sufficiently high concentrations (>20µM) stimulated state 4 and inhibited state 3 respiration. Stimulation of state 4 respiration was most pronounced for the carboxylic acids and the sulfonamides, which supports prior evidence that the perfluorinated carboxylic and acetic acids induce the mitochondrial permeability transition, whereas the sulfonamides are protonophoric uncouplers of oxidative phosphorylation. In both cases, potency increased with increasing carbon number, with a prominent inflection point between the six and eight carbon congeners. The results provide a foundation for classifying PFAAs according to specific modes of mitochondrial activity and, in combination with toxicokinetic considerations, establishing structure-activity-based boundaries for initial estimates of risk for noncancer endpoints for PFAAs for which minimal in vivo toxicity testing currently exists.

Detection and expression of enterotoxin genes in endophytic strains of Bacillus cereus.

AIMS: The aim of this study was to determine whether endophytic Bacillus cereus isolates from agronomic crops possessed genes for the nonhaemolytic enterotoxin (Nhe) and haemolysin BL (HBL) and, therefore, have the potential to cause diarrhoeal illness in humans. METHODS AND RESULTS: PCR followed by sequencing confirmed the presence of enterotoxin genes nheA, nheB, nheC, hblA, hblC, hblD in endophytic B. cereus. All nhe genes were detected in 59% of endophytic B. cereus, while all hbl genes were detected in 44%. All six genes were detected in 41% of isolates. Enterotoxin genes were not detected in 15% of B. cereus isolates. Reverse transcriptase real-time PCR confirmed that endophytic B. cereus could express enterotoxin genes in pure culture. CONCLUSIONS: This study showed that endophytic B. cereus isolates that possess genes for enterotoxin production are present in agronomic crops. Other endophytic B. cereus isolates lacked specific genes or lacked all nhe and hbl genes. Additionally, host, country of origin and tissue of origin had no impact on the enterotoxin genes detected. SIGNIFICANCE AND IMPACT OF THE STUDY: Bacillus cereus with the potential of causing diarrhoeal illness in humans is a cosmopolitan endophytic inhabitant of plants, not incidental surface inhabitants or contaminants, as often suggested by previous research.

Biochemical origins of the non-monotonic receptor-mediated dose-response.

A mathematical model was created to examine how xenobiotic ligands that bind to nuclear receptor proteins may affect transcriptional activation of hormone-regulated genes. The model included binding of the natural ligand (e.g. hormone) and xenobiotic ligands to the receptor, binding of the liganded receptor to receptor-specific DNA response sequences, binding of co-activator or co-repressor proteins (Rp) to the resulting complex, and the consequent transcriptional rate relative to that in the absence of the xenobiotic agent. The model predicted that the xenobiotic could act as a pure agonist, a pure antagonist, or a mixed agonist whose dose-response curve exhibits a local maximum. The response to the agent depends on the affinity of the liganded receptor-DNA complex for binding additional transcription factors (e.g. co-activator proteins). An inverted U-shaped dose-response occurred when basal levels of the natural ligand did not saturate receptor binding sites and the affinity for co-activator is weaker when the xenobiotic ligand is bound to the receptor than when the endogenous ligand is bound. The dose-response curve shape was not dependent on the affinity of the receptor for the xenobiotic agent; alteration of this value merely shifted the curve along the concentration axis. The amount of receptor, the density of DNA response sequences, and the affinity of the DNA-bound receptor for Rp determine the amplitude of the computed response with little overall change in curve shape. This model indicates that a non-monotonic dose-response is a plausible outcome for xenobiotic agents that activate nuclear receptors in the same manner as natural ligands.

A physiologically based pharmacokinetic model for inhalation and intravenous administration of naphthalene in rats and mice.

A diffusion limited physiologically based pharmacokinetic model for rats and mice was developed to characterize the absorption, distribution, metabolism, and elimination of naphthalene after inhalation exposure. This model includes compartments for arterial and venous blood, lung, liver, kidney, fat, and other organs. Primary sites for naphthalene metabolism to naphthalene oxide are the lung and the liver. The data used to create this model were generated from National Toxicology Program inhalation and iv studies on naphthalene and consisted of blood time-course data of the parent compound in both rats and mice. To examine the basis for possible interspecies differences in response to naphthalene, the model was extended to describe the distribution and metabolism of naphthalene oxide and the depletion and resynthesis of glutathione. After testing several alternative models, the one presented in this paper shows the best fit to the data with the fewest assumptions possible. The model indicates that tissue dosimetry of the parent compound alone does not explain why this chemical was carcinogenic to the female mouse lung but not to the rat lung. The species difference may be due to a combination of higher levels of naphthalene oxide in the mouse lung and a greater susceptibility of the mouse lung to epoxide-induced carcinogenesis. However, conclusions regarding which metabolite(s) may be responsible for the lung toxicity could not be reached.

Is peroxisome proliferation an obligatory precursor step in the carcinogenicity of di(2-ethylhexyl)phthalate (DEHP)?

Di(2-ethylhexyl)phthalate (DEHP), a peroxisome proliferator, has been listed by the International Agency for Research on Cancer (IARC) and by the National Toxicology Program as a possible or reasonably anticipated human carcinogen because it induces dose-related increases in liver tumors in both sexes of rats and mice. Recently, the suggestion has been advanced that DEHP should be considered unlikely to be a human carcinogen because it is claimed that the carcinogenic effects of this agent in rodents are due to peroxisome proliferation and that humans are nonresponsive to this process. An IARC working group recently downgraded DEHP to "not classifiable as to its carcinogenicity to humans" because they concluded that DEHP produces liver tumors in rats and mice by a mechanism involving peroxisome proliferation, which they considered to be not relevant to humans. The literature review presented in this commentary reveals that, although our knowledge of the mechanism of peroxisome proliferation has advanced greatly over the past 10 years, our understanding of the mechanism(s) of carcinogenicty of peroxisome proliferators remains incomplete. Most important is that published studies have not established peroxisome proliferation per se as an obligatory pathway in the carcinogenicity of DEHP. No epidemiologic studies have been reported on the potential carcinogenicity of DEHP, and cancer epidemiologic studies of hypolipidemic fibrate drugs (peroxisome proliferators) are inconclusive. Most of the pleiotropic effects of peroxisome proliferators are mediated by the peroxisome proliferator activated receptor (PPAR), a ligand-activated transcription factor that is expressed at lower levels in humans than in rats and mice. In spite of this species difference in PPAR expression, hypolipidemic fibrates have been shown to induce hypolipidemia in humans and to modulate gene expression (e.g., genes regulating lipid homeostasis) in human hepatocytes by PPAR activation. Thus, humans are responsive to agents that induce peroxisome proliferation in rats and mice. Because peroxisome proliferators can affect multiple signaling pathways by transcriptional activation of PPAR-regulated genes, it is likely that alterations in specific regulated pathways (e.g., suppression of apoptosis, protooncogene expression) are involved in tumor induction by peroxisome proliferators. In addition, because DEHP also induces biological effects that occur independently of peroxisome proliferation (e.g., morphologic cell transformation and decreased levels of gap junction intercellular communication), it is possible that some of these responses also contribute to the carcinogenicity of this chemical. Last, species differences in tissue expression of PPARs indicate that it may not be appropriate to expect exact site correspondence for potential PPAR-mediated effects induced by peroxisome proliferators in animals and humans. Because peroxisome proliferation has not been established as an obligatory step in the carcinogenicity of DEHP, the contention that DEHP poses no carcinogenic risk to humans because of species differences in peroxisome proliferation should be viewed as an unvalidated hypothesis.

Comparative carcinogenicity of 1,3-butadiene, isoprene, and chloroprene in rats and mice.

1,3-Butadiene, isoprene (2-methyl-1,3-butadiene), and chloroprene (2-chloro-1,3-butadiene) are high-production-volume chemicals used mainly in the manufacture of synthetic rubber. Inhalation studies have demonstrated multiple organ tumorigenic effects with each of these chemicals in mice and rats. Sites of tumor induction by these epoxide-forming chemicals were compared to each other and to ethylene oxide, a chemical classified by the National Toxicology Program (NTP) and by the International Agency for Research on Cancer (IARC) as carcinogenic to humans. For this group of chemicals, there are substantial species differences in sites of neoplasia; neoplasia of the mammary gland is the only common tumorigenic effect in rats and mice. Within each species, there are several common sites of tumor induction; these include the hematopoietic system, circulatory system, lung, liver, forestomach, Harderian gland, and mammary gland in mice, and the mammary gland and possibly the brain, thyroid, testis, and kidney in rats. For studies in which individual animal data were available, mortality-adjusted tumor rates were calculated, and estimates were made of the shape of the exposure-response curves and ED10 values (i.e. exposure concentrations associated with an excess risk of 10% at each tumor site). Most tumorigenic effects reported here were consistent with linear or supralinear models. For chloroprene and butadiene, the most potent response was for the induction of lung neoplasms in female mice, with ED10 values of 0.3 ppm. Based on animal cancer data, isoprene and chloroprene are listed in the NTP's Report on Carcinogens (RoC) as reasonably anticipated to be a human carcinogen. Butadiene is listed in the RoC as known to be a human carcinogen 'based on sufficient evidence of carcinogenicity from studies in humans, including epidemiological and mechanistic information', with support from experimental studies in laboratory animals. Epidemiology data for isoprene and chloroprene are not considered adequate to evaluate the potential carcinogenicity of these agents in humans.

Physiological modeling of butadiene disposition in mice and rats.

The earliest physiological models of 1,3-butadiene disposition reproduced uptake of the gas from closed chambers but over-predicted steady-state circulating concentrations of the mutagenic intermediates 1,2-epoxybut-3-ene and 1,2:3,4-diepoxybutane. A preliminary model based on the observation of a transient complex between cytochrome P450 and microsomal epoxide hydrolase on the endoplasmic reticulum membrane reproduced the blood epoxide concentrations as well as the chamber uptake data. This model was enhanced by the addition of equations for the production and detoxication of 3,4-epoxybutane-1,2-diol in the liver, lungs, and kidneys. The model includes flow-restricted delivery of butadiene and its metabolites to compartments for lungs, liver, fat, kidneys, gastrointestinal tract, other rapidly perfused tissues, and other slowly perfused tissues. Blood was distributed among compartments for arterial, venous, and tissue capillary spaces. Channeling of the three bound epoxides to epoxide hydrolase and their release from the endoplasmic reticulum are competing processes in this model. Parameters were estimated to fit data for chamber uptake of butadiene and epoxybutene, steady-state blood concentrations of epoxybutene and diepoxybutane, and the fractions of the inhaled dose of butadiene that appears as various excreted metabolites. The optimal values of the apparent K(m)s of membrane-bound epoxides for epoxide hydrolase were only 5% of the values for the cytosolic substrate, consistent with the observation of a transient complex between epoxide hydrolase and the cytochrome P450 that produces the epoxide. This proximity effect corresponds to the notion that epoxides produced in situ have privileged access to epoxide hydrolase. The model also predicts considerable accumulation of epoxybutanediol, in agreement with the observation that most of the DNA adducts in animals exposed to butadiene arise from this metabolite.

Point mutations of K-ras and H-ras genes in forestomach neoplasms from control B6C3F1 mice and following exposure to 1,3-butadiene, isoprene or chloroprene for up to 2-years.

1,3 Butadiene (BD), isoprene (IP) and chloroprene (CP) are structural analogs. There were significantly increased incidences of forestomach neoplasms in B6C3F1 mice exposed to BD, IP or CP by inhalation for up to 2-years. The present study was designed to characterize genetic alterations in K- and H-ras proto-oncogenes in a total of 52 spontaneous and chemically induced forestomach neoplasms. ras mutations were identified by restriction fragment length polymorphism, single strand conformational polymorphism analysis, and cycle sequencing of PCR-amplified DNA isolated from paraffin-embedded forestomach neoplasms. A higher frequency of K- and H-ras mutations was identified in BD-, IP- and CP-induced forestomach neoplasms (83, 70 and 57%, respectively, or combined 31/41, 76%) when compared to spontaneous forestomach neoplasms (4/11, 36%). Also a high frequency of H-ras codon 61 CAA-->CTA transversions (10/41, 24%) was detected in chemically induced forestomach neoplasms, but none were present in the spontaneous forestomach neoplasms examined. Furthermore, an increased frequency (treated 13/41, 32% versus untreated 1/11, 9%) of GGC-->CGC transversion at K-ras codon 13 was seen in BD-, and IP-induced forestomach neoplasms, similar to the predominant K-ras mutation pattern observed in BD-induced mouse lung neoplasms. These data suggest that the epoxide intermediates of the structurally related chemicals (BD, IP, and CP) may cause DNA damage in K-ras and H-ras proto-oncogenes of B6C3F1 mice following inhalation exposure and that mutational activation of these genes may be critical events in the pathogenesis of forestomach neoplasms induced in the B6C3F1 mouse.

Carcinogenesis bioassays: study duration and biological relevance.

Criticisms of the scientific value of rodent carcinogenicity bioassays have focused on the arguments that the studies are too long and that most organ-specific carcinogenic effects observed in experimental animals have little or no relevance to humans. For example, Davies et al. (Davies, T.S., Lynch, B.S., Monro, A.M., Munro, I.C., Nestmann, E.R., 2000. Rodent carcinogenicity tests need be no longer than 18 months: an analysis based on 210 chemicals in the IARC Monographs. Food and Chemical Toxicology 38, 219-235) concluded that the duration of rodent bioassays should be no more than 18 months, based on their analysis of 210 International Agency for Research on Cancer (IARC) rodent carcinogens in which they report that most chemicals showed "tumorigenic effects" at or before 12 months. However, many of these "tumorigenic effects" reflect the occurrence of a single neoplasm, with most tumors occurring much later in the study. Reliance on a single tumor at an early time point as providing definitive evidence of rodent carcinogenicity is a dangerous practice that could produce both false positive and false negative outcomes. An extensive evaluation of the NTP database reveals that many rodent carcinogens produce later-appearing tumors that would not be detected as statistically significant in a 12-18 month study. Such a shortened duration study would be roughly equivalent to evaluating human cancer in subjects 30-50 years of age, which would result in markedly reduced study sensitivity. In fact, many investigators recommend extending the duration of rodent studies to 30 months or to a true lifetime to increase study sensitivity. We also do not agree with the second conclusion of Davies et al. (2000) that the mode of action of rodent carcinogenesis is sufficiently well understood to justify discounting the majority of organ-specific carcinogenic effects found in these studies. The consequences of performing rodent carcinogenicity studies with inadequate sensitivity, and then discounting most of the carcinogenic effects that are observed will be that potential human carcinogens will not be detected, thus forcing near total reliance on human studies for this purpose. This is not prudent public health policy.

Alleged misconceptions' distort perceptions of environmental cancer risks.

In a series of papers, Ames and colleagues allege that the scientific and public health communities have perpetuated a series of 'misconceptions' that resulted in inaccurate identification of chemicals that pose potential human cancer risks, and misguided cancer prevention strategies and regulatory policies. They conclude that exposures to industrial and synthetic chemicals represent negligible cancer risks and that animal studies have little or no scientific value for assessing human risks. Their conclusions are based on flawed and untested assumptions. For instance, they claim that synthetic residues on food can be ignored because 99.99% of pesticides humans eat are natural, chemicals in plants are pesticides, and their potential to cause cancer equals that of synthetic pesticides. Similarly, Ames does not offer any convincing scientific evidence to justify discrediting bioassays for identifying human carcinogens. Ironically, their arguments center on a ranking procedure that relies on the same experimental data and extrapolation methods they criticize as being unreliable for evaluating cancer risks. We address their inconsistencies and flaws, and present scientific facts and our perspectives surrounding Ames' nine alleged misconceptions. Our conclusions agree with the International Agency for Research on Cancer, the National Toxicology Program, and other respected scientific organizations: in the absence of human data, animal studies are the most definitive for assessing human cancer risks. Animal data should not be ignored, and precautions should be taken to lessen human exposures. Dismissing animal carcinogenicity findings would lead to human cancer cases as the only means of demonstrating carcinogenicity of environmental agents. This is unacceptable public health policy.

The privileged access model of 1,3-butadiene disposition.

In previous attempts to model disposition of 1,3-butadiene in mice and rats, parameter values for 1,2-epoxybut-3-ene metabolism were optimized to reproduce elimination of this gas from closed chambers. However, each of these models predicted much higher concentrations of circulating epoxybutene than were subsequently measured in animals exposed to butadiene. To account for this discrepancy, a previous physiologically based pharmacokinetic model of butadiene disposition was modified to describe a transient complex between cytochrome P450 and epoxide hydrolase on the endoplasmic reticulum membrane. In this model the epoxide products are directly transferred from the P450 to the epoxide hydrolase in competition with release of products into the cytosol. The model includes flow-restricted delivery of butadiene and epoxides to gastrointestinal tract, liver, lung, kidney, fat, other rapidly perfused tissues, and other slowly perfused tissues. Blood was distributed among compartments for arterial, venous, and capillary spaces. Oxidation of butadiene and epoxybutene and hydrolysis and glutathione conjugation of epoxides were included in liver, lung, and kidney. The model reproduces observed uptake of butadiene and epoxybutene from closed chambers by mice and rats and steady-state concentrations of butadiene, epoxybutene, and 1,2;3,4-diepoxybutane concentrations in blood of mice and rats exposed by nose only. Successful replication of these observations indicates that the proposed privileged access of epoxides formed in situ to epoxide hydrolase is a plausible mechanistic representation for the metabolic clearance of epoxide-forming chemicals.

Mutations of ras protooncogenes and p53 tumor suppressor gene in cardiac hemangiosarcomas from B6C3F1 mice exposed to 1,3-butadiene for 2 years.

1,3-Butadiene is a multisite carcinogen in rodents. Incidences of cardiac hemangiosarcomas were significantly increased in male and female B6C3F1 mice that inhaled 1,3-butadiene (BD) for 2 years. Eleven BD-induced cardiac hemangiosarcomas were examined for genetic alterations in ras protooncogenes and in the p53 tumor suppressor gene. Nine of 11 (82%) BD-induced hemangiosarcomas had K-ras mutations and 5 of 11 (46%) had H-ras mutations. All of the K-ras mutations were G-->C transversions (GGC-->CGC) at codon 13; this pattern is consistent with reported results in BD-induced lung neoplasms and lymphomas. Both K-ras codon 13 CGC mutations and H-ras codon 61 CGA mutations were detected in 5 of 9 (56%) hemangiosarcomas. The 11 hemangiosarcomas stained positive for p53 protein by immunohistochemistry and were analyzed for p53 mutations using cycle sequencing of polymerase chain reaction (PCR) amplified DNA isolated from paraffin-embedded sections. Mutations in exons 5 to 8 of the p53 gene were identified in 5 of 11 (46%) hemangiosarcomas, and all of these were from the 200- or 625-ppm exposure groups that also had K-ras codon 13 CGC mutations. Our data indicate that K-ras, H-ras, and p53 mutations in these hemangiosarcomas most likely occurred as a result of the genotoxic effects of BD and that these mutations may play a role in the pathogenesis of BD-induced cardiac hemangiosarcomas in the B6C3F1 mouse.

Dose-response analyses of experimental cancer data.

Dose-response analysis provides a powerful tool to determine causality from experimental cancer data, estimate low-dose risk, and evaluate mechanistic hypotheses. However, the interpretation of cancer dose-response data can be influenced by how the dose and response terms are characterized. Using the poly-3 quantal response method to adjust for the extensive and early development of lethal lymphomas in butadiene-exposed mice provided a means of obtaining a better representation of dose-response relationships for late-developing tumors induced by this chemical. Fitting a Weibull model to survival-adjusted tumor data for chloroprene and butadiene indicated similar carcinogenic potencies for these chemicals in mice. In conjunction with the rodent toxicity and carcinogenicity studies conducted by the National Toxicology Program, toxicokinetic studies are performed to characterize relationships between exposure and tissue concentrations of parent compound and metabolites. A physiologically based pharmacokinetic model (PBPK) of butadiene dosimetry indicated that differences in carcinogenic response between rats and mice are not simply due to differences in tissue concentrations of epoxybutene, a mutagenic metabolic intermediate. Thus, factors beyond tissue dosimetry of this metabolite must be important in butadiene-induced carcinogenesis. A PBPK model for isoprene indicated that blood concentrations of isoprene epoxides are a better indicator of kidney cancer risk than are measurements of isoprene-exposure concentrations. An evaluation of dose-response relationships for cytotoxicity, regenerative hyperplasia, and tumor induction by trihalomethanes indicates that for this family of chemicals, cell proliferation is not a reliable predictor of tumor response.

Examination of low-incidence brain tumor responses in F344 rats following chemical exposures in National Toxicology Program carcinogenicity studies.

Neoplasms in the brain are uncommon in control Fischer 344 (F344) rats; they occur at a rate of less than 1% in 2-yr toxicity/carcinogenicity studies. Furthermore, only 10 of nearly 500 studies conducted by the National Toxicology Program (NTP) showed any evidence of chemically related neoplastic effects in the brain. Generally, the brain tumor responses were considered equivocal, because the characteristics of potential neurocarcinogenic agents (such as statistically significant increased incidences, decreased latency and/or survival, and demonstration of dose-response relationships) were not observed. A thorough examination, including comparisons with a well-established historical database, is often critical in evaluating rare brain tumors. Chemicals that gave equivocal evidence of brain tumor responses were generally associated with carcinogenicity at other sites, and many chemicals were mutagenic when incubated with metabolic activating enzymes. Other factors that were supportive of the theory that marginal increases in brain tumor incidence were related to chemical exposure were that (a) some of the tumors were malignant, (b) no brain neoplasms were observed in concurrent controls from some studies, and/or (c) brain tumors were also seen following exposure to structurally related chemicals. In 2-yr studies in F344 rats (studies conducted by the NTP), equivocal evidence of carcinogenicity was observed for the following 9 chemicals: isoprene, bromoethane, chloroethane, 3,3'-dimethylbenzidine dihydrochloride, 3,3'-dimethoxybenzidine dihydrochloride, furosemide, C.I. direct blue 15, diphenhydramine hydrochloride, and 1-H-benzotriazole. Glycidol was the only chemical evaluated by the NTP with which there was clear evidence of brain tumor induction in F344 rats. Clarification of the potential neurocarcinogenic risks of chemicals that produce equivocal evidence of a brain tumor response in conventional 2-yr rodent studies may be aided by the use of transgenic mouse models that exhibit genetic alterations that reflect those present in human brain tumors as well as by the use of in utero exposures.

A physiological model for ligand-induced accumulation of alpha 2u globulin in male rat kidney: roles of protein synthesis and lysosomal degradation in the renal dosimetry of 2,4,4-trimethyl-2-pentanol.

A physiologically based pharmacokinetic (PBPK) model was constructed for the disposition of 2,4,4-trimethyl-2-pentanol (TMP-2-OH) in male rats and its induction of accumulation of renal alpha2u-globulin (alpha2u). The model included diffusion-restricted delivery of TMP-2-OH to compartments representing liver, lung, fat, kidney, GI tract, aggregated rapidly perfused tissues, and aggregated slowly perfused tissues. Metabolism by oxidation and glucuronidation was included for liver and kidneys. Rates of hepatic alpha2u production and resorption by renal proximal tubules were taken from the literature. Degradation of liganded alpha2u by renal lysosomal cathepsins was modeled with a Km value corresponding to the measured 30% reduction in proteolytic efficiency and with free and bound forms of alpha2u competing for access to the enzymes. Increased pinocytotic uptake of alpha2u into the kidney induces cathepsin activity. A model that ascribed renal alpha2u accumulation solely to reduced lysosomal proteolysis failed to reproduce the observed accumulation. The model could reproduce experimental observations if a transient increase in hepatic synthesis of alpha2u, stimulated by the presence of liganded alpha2u in the blood, and accelerated secretion of the protein from the liver were assumed. This model reproduces time course data of blood and kidney TMP-2-OH and renal alpha2u concentrations, suggesting that renal accumulation of alpha2u is not simply a consequence of reduced proteolytic degradation but may also involve a transient increase in hepatic alpha2u production. The model predicts increased delivery of TMP-2-OH to the kidney and consequent increased renal production of potentially toxic TMP-2-OH metabolites than would be the case if no alpha2u were present. Induced lysosomal activity and increased production of toxic metabolites may both contribute to the nephrotoxicity observed in male rats exposed to an alpha2u ligand or its precursor.

High frequency of codon 61 K-ras A-->T transversions in lung and Harderian gland neoplasms of B6C3F1 mice exposed to chloroprene (2-chloro-1,3-butadiene) for 2 years, and comparisons with the structurally related chemicals isoprene and 1,3-butadiene.

Chloroprene is the 2-chloro analog of 1,3-butadiene, a potent carcinogen in laboratory animals. Following 2 years of inhalation exposure to 12.8, 32 or 80 p.p.m. chloroprene, increased incidences of lung and Harderian gland (HG) neoplasms were observed in B6C3F1 mice at all exposure concentrations. The present study was designed to characterize genetic alterations in the K- and H-ras proto-oncogenes in chloroprene-induced lung and HG neoplasms. K-ras mutations were detected in 80% of chloroprene-induced lung neoplasms (37/46) compared with only 30% in spontaneous lung neoplasms (25/82). Both K- and H-ras codon 61 A-->T transversions were identified in 100% of HG neoplasms (27/27) compared with a frequency of 56% (15/27) in spontaneous HG neoplasms. The predominant mutation in chloroprene-induced lung and HG neoplasms was an A-->T transversion at K-ras codon 61. This mutation has not been detected in spontaneous lung tumors of B6C3F1 mice and was identified in only 7% of spontaneous HG neoplasms. In lung neoplasms, greater percentages (80 and 71%) of A-->T transversions were observed at the lower exposures (12.8 and 32 p.p.m.), respectively, compared with 18% at the high exposure. In HG neoplasms, the percentage of A-->T transversions was the same at all exposure concentrations. The chloroprene-induced ras mutation spectra was similar to that seen with isoprene, where the predominant base change was an A-->T transversion at K-ras codon 61. This differed from 1,3-butadiene, where K-ras codon 13 G-->C transitions and H-ras codon 61 A-->G transitions were the predominant mutations. The major finding of K-ras A-->T transversions in lung and Harderian gland neoplasms suggests that this mutation may be important for tumor induction by this class of carcinogens.

Multiple organ carcinogenicity of inhaled chloroprene (2-chloro-1,3-butadiene) in F344/N rats and B6C3F1 mice and comparison of dose-response with 1,3-butadiene in mice.

Chloroprene (2-chloro-1,3-butadiene) is a high production chemical used almost exclusively in the production of polychloroprene (neoprene) elastomer. Because of its structural similarity to 1,3-butadiene, a trans-species carcinogen, inhalation studies were performed with chloroprene to evaluate its carcinogenic potential in rats and mice. Groups of 50 male and female F344/N rats and 50 male and female B6C3F1 mice were exposed to 0, 12.8, 32 or 80 p.p.m. chloroprene (6 h/day, 5 days/week) for 2 years. Under these conditions, chloroprene was carcinogenic to the oral cavity, thyroid gland, lung, kidney and mammary gland of rats, and to the lung, circulatory system (hemangiomas and hemangiosarcomas), Harderian gland, kidney, forestomach, liver, mammary gland, skin, mesentery and Zymbal's gland of mice. Survival adjusted tumor rates in mice were fit to a Weibull model for estimation of the shape of the dose-response curves, estimation of ED10 values (the estimated exposure concentration associated with an increased cancer risk of 10%) and comparison of these parameters with those for 1,3-butadiene. Butadiene has been identified as a potent carcinogen in mice and has been associated with increased risk of lymphatic and hematopoietic cancer in exposed workers. Shape parameter values for most of the neoplastic effects of chloroprene and 1,3-butadiene were consistent with linear or supralinear responses in the area near the lowest tested exposures. The most potent carcinogenic effect of 1,3-butadiene was the induction of lung neoplasms in female mice, which had an ED10 value of 0.3 p.p.m. Since the ED10 value for that same response in chloroprene exposed mice was also 0.3 p.p.m., we conclude that the carcinogenic potency of chloroprene in mice is similar to that of 1,3-butadiene. Cancer potency of chloroprene is greater in the mouse lung than in the rat lung, but greater in the rat kidney than in the mouse kidney and nearly equivalent in the mammary gland of each species.