The role of genetic polymorphisms in environmental health. (Research Review).
With the initial completion of the first draft of the human genome sequence (Lander et al. 2001; Venter et al. 2001), interest has dramatically increased in the role of genetics as a determinant of health. Progress in incorporating genetics into public health research has been steady over the last several years, relying mainly on the tools of genetic and molecular epidemiology. Research exploring the role of genetics in determining susceptibility to environmentally induced disease has also grown. The recent abundance of epidemiologic research examining associations between polymorphic genes that code for enzymes involved in xenobiotic biotransformation and disease has on occasion generated interesting findings. However, the approach used in these studies differs substantially from that of traditional environmental health science research. Whereas traditional environmental health sciences seek to understand the effect of exposure of a homogeneous population to some agent, many of the recent genetic and molecular epidemiologic studies have been structured to analyze gene-disease associations, regardless of exposure. In addition, many of the findings have not been replicated in subsequent studies, casting doubt on their validity and leaving the environmental health community with uncertain results with which to proceed.
In this review, we present a general introduction of this evolving area of research on gene-environment interactions for environmental health practitioners and students. We begin by assessing the integration of genetics into environmental health research using the same exposure [right arrow] disease paradigm traditionally used by environmental health scientists, adding genetics to the existing paradigm as a potential modifier of dose or effect of the initial exposure. Then we discuss selected examples of gene-environment interaction from the literature, classifying them into one of three categories on the basis of evidence from laboratory and epidemiologic data. Finally, we describe the benefits of applying this model to future research efforts, and we offer a basic framework for investigators wishing to pursue this type of endeavor.
Environmental Exposures and Human Genetic Variation
Much of the impetus for this area of research has come from pharmacogenetics, which is concerned primarily with the study of genetic variation in drug efficacy and toxicity. It has been recognized for many decades that individual differences in response to pharmacologic treatment, exhibited as drug toxicity or a lack of therapeutic effect, are often caused by genetic differences that result in altered rates of biotransformation (metabolism). Notable examples include nerve damage among individuals homozygous for some variants of the N-acetyltransferase 2 gene ("slow acetylators") given isoniazid as an antituberculosis therapy, hemolytic anemia among glucose 6-phosphate dehydrogenase-deficient patients given aminoquinoline antimalarial drugs, and varied rates of biotransformation of debrisoquine, an antihypertensive drug, due to genetic variation at the CYP2D6 locus (Weber 1997).
The process of biotransformation--the enzymatic alteration of foreign or xenobiotic compounds--is conventionally divided into two phases. Phase I enzymes introduce new (or modify existing) functional groups (e.g., -OH, -SH, -N[H.sub.3]) to xenobiotics and are catalyzed primarily by the cytochrome P450 enzymes (CYPs), although numerous other oxidases, reductases, and dehydrogenases may also participate. These intermediates are then conjugated with endogenous ligands during phase II, increasing the hydrophilic nature of the compound, facilitating excretion. Enzymes involved in phase II include the N-acetyltransferases (NATs), glutathione S-transferases (GSTs), UDP glucuronosyltransferases, epoxide hydrolases, and methyltransferases. Phase I and II reactions are catalyzed by enzymes collectively known as xenobiotic metabolism enzymes (XMEs). XMEs are most abundant in the liver, although most tissues have some XME activity. A balance between phase I and II enzymes is generally necessary to promote the efficient detoxification and elimination of xenobiotics, thereby protecting the body from injury caused by exposure (Parkinson 1997). More recently, the role of drug transporters (e.g., P-glycoprotein) in influencing xenobiotic disposition has been highlighted. These transporters facilitate the excretion of xenobiotics into bile or blood (Silverman 2000), and thus form what has been called phase III biotransformation.
Sequence variations (in the past often referred to as mutations) in the genes encoding these enzymes and other proteins result from stochastic genetic processes and may accumulate in the population, depending on selective pressures. If the frequency of a specific sequence variant reaches 1% or more in the population, it is referred to as a polymorphism, and a frequency of 10% or more is typically thought of as common. Alternate versions of genes containing different sequence variants are known as alleles (Harris 1980). The resulting patterns of variation in a gene or chromosome form what is known as a haplotype, and a proposal for a nomenclature system to aid in the designation of haplotypes has recently been given (Nebert 2002).
A polymorphism may have no effect (i.e., is "silent"), or it may be considered functional if it results in altered catalytic function, stability, and/or level of expression of the resulting protein. Functional polymorphisms in XMEs include a) point mutations in coding regions of genes resulting in amino acid substitutions, which may alter catalytic activity, enzyme stability, and/or substrate specificity; b) duplicated or multiduplicated genes, resulting in higher enzyme levels; c) completely or partially deleted genes, resulting in no gene product; and d) splice site variants that result in truncated or alternatively spliced protein products (Ingelman-Sundberg et al. 1999). Polymorphisms in the regulatory regions of genes may affect the amount of protein expression as well, and mutations in other noncoding regions may affect mRNA stability or mRNA splicing. Most research in genetics in environmental health has focused on these types of functional variants.
About 90% of all DNA sequence variations occur as single nucleotide polymorphisms (SNPs)--that is, single-base-pair substitutions (the first type of functional variant, point mutations) (Brookes 1999). As of March 2002, more than 1,255,000 SNPs have been identified and catalogued as a result of multiple research efforts (SNPs Consortium 2002). There are estimated to be three or four SNPs in the average gene and roughly 120,000 common coding-region SNPs, of which approximately 40% are expected to be functional (Cargill et al. 1999). These estimates do not include variants outside the coding region of genes, and therefore the total number of SNPs affecting protein function can be expected to be greater.
Functional polymorphisms in XMEs can affect the balance of metabolic intermediates produced during biotransformation, and some of these intermediates can bind and induce structural changes in DNA or binding other critical macromolecules, such as sulfhydryl-containing proteins. Similarly, polymorphisms in DNA repair enzymes can affect an individual's ability to repair DNA damage induced by some exposures, such as ultraviolet radiation. The interindividual differences in these and other components of the human genome that relate to environmental exposures have therefore been predicted to modify environmental disease risk (Perera 1997). In addition to polymorphisms, age, sex, hormones, and behavioral factors such as cigarette smoking, alcohol consumption, and nutritional status can influence the expression of phase I and II biotransformation genes (Levy 2000) and thus are also important in understanding environmental disease risk.
One can contrast the role of polymorphisms in XMEs and other components of the environmental response system with variants that are highly penetrant (i.e., that almost invariably lead to disease) but have low population frequency. The interest and focus here are on the role of common sequence variants that alter the effect of exposures that may lead to disease states, or their precursors, and hence are of lower penetrance. Although the individual risk associated with these polymorphisms is often low, they potentially have greater public health relevance (i.e., population-attributable risk) because of their high population frequency (Caporaso and Goldstein 1995).
A comprehensive effort to identify polymorphisms in genes involved in environmentally induced disease, known as the Environmental Genome Project (EGP), was initiated by the National Institute of Environmental Health Sciences (NIEHS) in 1998 (Olden and Wilson 2000). In addition to the identification of polymorphisms, the EGP aims to characterize the function of these polymorphisms and supports epidemiologic studies of gene-environment interactions as well. Like the Human Genome Project, the EGP has devoted substantial resources to the ethical, legal, and social issues related to this project.
Examples of Genetic Effect Modifiers
The working hypothesis typically employed is that for most polymorphisms that alter responses to chemical hazards, the genetic difference does not produce a qualitatively different response, but rather induces a shift in the dose-response relationship. Thus, for example, a polymorphism in an XME that decreases the catalytic efficiency of an enzyme that detoxifies a particular drug might make the standard dose of that drug toxic. This concept extends not only to the acute effects of drugs, but also potentially to chronic response to nondrug chemicals found in the workplace and general environment. Below we describe several examples of gene-environment interaction that illustrate the potential public health implications, as well as difficulties in interpretation, of this type of research.
The relationship between aromatic amine exposure, N-acetyltransferase 2 polymorphism (NAT2), and bladder cancer is a classic illustration of the principle of dose-effect modification of an environmental exposure by polymorphisms. An initial study by Lower et al. (1979) suggested that the effect of exposure to aromatic amines (bladder cancer), by occupation (e.g., dye industry) or smoking, differed by NA T2 phenotype. A preponderance of slow acetylators existed among exposed persons, and subsequent studies have confirmed these results (Cartwright et al. 1982; Hanke and Krajewska 1990).
Recently, Marcus and colleagues conducted a meta-analysis of acetylation status and bladder cancer risk case-control studies (Marcus et al. 2000a) and a case-series meta-analysis of 16 studies of the NAT2x smoking interaction in bladder cancer (Marcus et al. 2000b). Across all studies, they calculated an odds ratio (OR) of 1.3 [95% confidence interval (CI), 1.0-1.6] for smokers who are slow acetylators compared with smokers who are rapid acetylators, verifying that smokers who are slow acetylators have a modestly increased risk (Marcus et al. 2000b). Limiting the study selection to European studies with large sample sizes (number of cases [is greater than or equal to] 150), the OR was 1.7 (95% CI, 1.2-2.3). Different patterns of tobacco use and tobacco type may account for some of these differences. In addition, using estimates of the prevalence of smoking and NAT2 genotype, Marcus et al. (2000b) predicted bladder cancer risk for smokers and nonsmokers by acetylator status, designating never-smoker rapid acetylators as the reference category. Nonsmoking slow acetylators were predicted to have no increase in risk (OR = 1.10), ever-smoking rapid acetylators have about two times the risk (OR = 1.95), and ever-smokers who are slow acetylators have about 3-fold higher risk (OR = 3.21). Marcus et al. (2000b) also estimated that the population-attributable risk of the gene-environment interaction was 35% for slow acetylators who had ever smoked and 13% for rapid acetylators who had ever smoked.
In the laboratory setting, complementary experiments can be designed to gain understanding of the biologic basis of the observed effect. This ultimately contributes to the argument of causality. Primary human cell lines, transient and stable transfection assays in cell lines, and transgenic animal models have frequently been used to investigate these questions. With respect to aromatic amines, NAT2, and bladder cancer, in vitro and in vivo studies have demonstrated that polymorphic N-acetylation of some aromatic amines can bioactivate these procarcinogens in the bladder (Hein et al. 1993; Mattano et al. 1989; Trinidad et al. 1990). After N-oxidation of aromatic amines such as 4-aminobiphenyl or 2-naphthylamine by CYP1A2 in the liver, O-acetylation of the resulting hydroxylamine by NAT2 can produce unstable acetoxy esters that decompose to form highly electrophilic aryl nitrenium ion species. In addition, the formation of the acetoxy ester, a proximate carcinogen, can proceed through N-acetylation and N-oxidation reactions that yield N-hydroxy-N-acetyl aromatic amines, which then form the acetoxy ester through N, O-acetyltransferase catalyzed by NAT2. In slow acetylators, initial acetylation in the liver is less efficient, and hence biotransformation of the aromatic amine is more likely to proceed through the CYP1A2 route. Subsequently, the hydroxylated aromatic amine can be further bioactivated in the bladder, either enzymatically or nonenzymatically, potentially leading to DNA binding and point mutations. This is considered a likely mechanism of initiation of bladder carcinogenesis (Autrup 2000; Colvin et al. 1998; Williams 2001). Thus, after the early findings by Lower et al. (1979), the concerted efforts of epidemiologic and toxicologic studies have quantitatively evaluated this gene-environment interaction and elucidated a probable mechanism.
Recent research exploring genetic modifiers of other common exposures with significant public health importance have begun to yield interesting findings. In addition to gene-environment interactions that link exposures, polymorphisms, and disease states, associations of particular exposures with biomarkers of exposure or effect and polymorphic variants have been evaluated. To broadly describe the status of this research, we compiled a nonexhaustive list of these exposures and biomarkers or diseases with their potential genetic effect modifiers, shown in Table 1, by searching the published literature (see Appendix 1 for additional information about the genes). As an exercise to identify gaps in knowledge about the exposure-disease association and effect modification that merit further investigation, we then classified the evidence for these relationships according to the following system: 3, associations proposed from basic scientific laboratory reports; 2, associations with laboratory evidence and suggestive epidemiologic data; 1, associations with laboratory evidence and supporting epidemiologic data.
Table 1 shows several different types of exposures, including exposures to industrially produced compounds and by-products (e.g., butadiene and dioxin), substances in the diet (e.g., alcohol and aflatoxin [B.sub.1]), and both voluntary and involuntary examples of exposure (e.g., tobacco smoke and environmental tobacco smoke). As would be expected, some genes appear to be associated with several different exposures. This can be attributed partially to the relatively nonspecific roles of their gene products in biotransformation of exogenous substrates. It is also likely that once genotyping methods for a particular gene have been developed and streamlined, its role in several pathways will be explored. In total, based on our review of the published literature, we gave few examples in Table 1 a classification of 1, which indicates that evidence clearly demonstrating effect modification by polymorphisms is quite limited.
An example of the evolving knowledge of effect modification by polymorphisms is that of exposure to aflatoxin [B.sub.1], a mycotoxin found in some foodstuffs, and an established risk for hepatocellular carcinoma (HCC), especially when combined with hepatitis virus exposure (Ross et al. 1992). The biotransformation of aflatoxin [B.sub.1] proceeds through a CYP450-mediated oxidation and then through reactions catalyzed by GST, epoxide hydrolase, and/or glucuronosyltransferase to yield excretable metabolites (Eaton and Groopman 1994). For exposed persons, having GSTM1 and EPHX1 (epoxide hydrolase 1) genotypes conferring a lack of enzyme and less active enzyme, respectively, was shown to result in increased HCC risk (London et al. 1995; McGlynn et al. 1995). Similarly, functional variants in CYP1A2 and CYP3A4, both of which catalyze the phase I metabolism (epoxidation) of aflatoxin [B.sub.1], would also be expected to modify HCC risk in exposed persons, although epidemiologic data for this have not yet been gathered. Biomarker studies of urinary aflatoxin metabolites and aflatoxin--albumin adducts in peripheral blood have validated their use as indicators of HCC risk at the group level, and polymorphisms in GSTM1 and EPHX1 yielded higher levels of adducts (Wild and Turner 2001). Thus, in the case of aflatoxin, exposure-specific, validated biomarkers can be used in lieu of clinical disease measures to estimate the effect modification by specific variants. Even for this example, however, only a few studies exist, and they have limited statistical power; hence, the magnitude of the modifying effect of polymorphisms remains highly uncertain. Future efforts to determine the predictive value of biomarkers of other exposures will facilitate the analysis of the effects of polymorphisms in modifying the effects of those exposures.
Contradictory findings are often found in the literature. Similar issues have been encountered in pharmacogenetic studies. Evans and Relling (1999) have commented that the use of different end points in assessing response to drugs, the heterogeneous nature of diseases studied, and the polygenic nature of many drug effects all contribute to the study-to-study variation often observed. These same factors will also be important in types of studies discussed here. Additionally, there is controversy regarding the issue of population stratification, or bias in estimate of association between a polymorphism and disease because of confounding of a true risk factor with ethnicity (Thomas and Witte 2002; Wacholder et al. 2002), as it relates to study-to-study variation. Wacholder et al. (2000) have shown that well-designed Case--control and cohort studies of cancer are free of significant bias due to population stratification. The debate, however, remains contentious.
The examples of gene-environment interaction presented thus far have been fairly simple. More realistically, chronic disease risk is a function of multiple genes interacting with each other and with multiple environmental factors over a lifetime. Taylor et al. (1998) provided evidence for a three-way interaction between NAT2, NAT1, and smoking that modifies bladder cancer risk such that individuals who smoke and have NAT2 slow acetylator alleles in combination with the high-activity NVAT1*10 allele (homozygotes or heterozygotes) have heightened bladder cancer risk. Contrasting findings, however, have been reported more recently (Cascorbi et al. 2001).
Advantages of Incorporating Polymorphisms into Health Effects Studies
The addition of polymorphisms affords several noteworthy opportunities for health effects studies of exposures to environmental toxicants and toxins. Stratification of a studied health outcome or biomarker by relevant genotype (or phenotype) may allow for detection of different levels of risk among subgroups of exposed persons (Rothman et al. 2001). Collectively, the studies on aromatic amine exposure, NAT2 genotype, and bladder cancer demonstrate this point. Investigations that assess bladder cancer risk associated with exposure to aromatic amines alone would observe a magnitude of effect that represents the average risk for rapid and slow acetylators combined. This estimate would not suggest that aromatic amines are as etiologically significant, that is, are potent carcinogens, for particular subpopulations, as a stratified analysis would indicate. This has been referred to as effect dilution (Khoury et al. 1993). Effect dilution may be especially important for common exposures--to dietary constituents or air pollution, for example--whose association to a disease outcome is often weak.
Second, evidence of effect modification by genotype yields insights into the potential biologic processes of toxicity or carcinogenicity, as substrates or targets of candidate gene products are identified as potential causative agents (Rothman et al. 2001). The effect of lipopolysaccharide (LPS; also known as endotoxin), a component of particulate matter in rural areas, on lung function parameters may turn out to be a modern example of this. Arbour et al. (2000) have shown that response to LPS, measured by decrease in forced expiratory volume in the first second (FEV1), differed by TLR4 genotype. TLR4 codes for the toll-like receptor that binds LPS and initiates a signal transduction pathway that leads to inflammation of the lung. Their data suggest that individuals with the variant TLR4 genotype may be resistant to LPS-induced lung inflammation but may be more susceptible to a systemic inflammatory response. These findings may aid in answering the difficult question of what component(s) of particulate matter is responsible for the range of health effects observed, particularly in rural areas where LPS levels are appreciable.
Finally, enhanced understanding of pathologic mechanism gained by the concerted efforts of epidemiologic and toxicologic studies may allow for the development of drugs or dietary interventions that prevent disease onset or progression. As an example, oltipraz [OPZ; 5-(2-pyrazinyl)-4-methyl- 1,2-dithiole-3-thione] is a drug that induces phase II XMEs, notably the GSTs (Carr and Franklin 1998). Early evidence showed that OPZ can protect against the hepatocarcinogenic effects of aflatoxin [B.sub.1] in rats, and subsequent efforts have demonstrated that administration of OPZ to humans significantly enhanced excretion of a phase II product, aflatoxin--mercapturic acid (Kensler et al. 2000). Interestingly, there is also evidence that OPZ may act by competitively inhibiting CYP1A2, thereby preventing the activation of aflatoxin (Langouet et al. 1995). In total, the understanding of aflatoxin biotransformation pathways from animal models and in vitro human tissue studies led to the hypothesis-based epidemiologic studies and ultimately contributed to the development of a chemoprevention strategy for aflatoxin-induced HCC.
Additionally, studies on the health effects of exposure to regulated environmental contaminants that incorporate genetic susceptibilities will enlarge the body of knowledge pertaining to the range of human variability in response to these contaminants. For example, the National Report on Human Exposure to Environmental Chemicals (CDC 2001) reports body burden among National Health and Nutrition Examination Study (NHANES) subjects for 27 chemicals. Studies developed to look at the effect of these chemicals should include genes that might confer susceptibility. In this way, the risk assessment process may be improved by using refined estimates of human variability instead of the default assumptions conventionally used (i.e., uncertainty factor of 10), potentially improving public health protection and the regulation of industry through redefinition of acceptable exposure levels. This advantage has been touted for some time, but no clear example yet exists of how this can be done, especially in the face of numerous ethical, legal, and social issues surrounding the use of genetic information. Still, the promise holds, and the potential continues to grow as more functional variants are discovered and their roles in effect modification are deduced.
In the environmental health community, discussion of the issue of focusing disease prevention efforts on genetically susceptible individuals has begun, with an emphasis on the inherently complex ethical, legal, and social issues. Researchers at the University of Washington's Center for Ecogenetics and Environmental Health (Burke W. Personal communication) and at the University of Cincinnati Center for Environmental Genetics (Vandale and Bingham 2000) are devoting considerable efforts to exploring these issues using case studies. In addition, the University of Washington Institute for Public Health Genetics and the University of Michigan Public Health Genetics Interdepartmental Concentration offer public health students the opportunity to learn about these issues.
For environmental health scientists interested in pursuing health effects research that incorporates genetic effect modifiers, we describe a framework for an investigation that includes polymorphisms. This framework assumes that the investigator(s) already has chosen the study design. Case--control and cohort studies are used most often to evaluate gene-environment interaction, and their benefits and drawbacks have been compared and contrasted (Caporaso et al. 1999; Langholz et al. 1999).
Exposure assessment. Exposure assessment is of paramount importance in studies of gene-environment interaction. Typically, efforts aim to characterize the type, duration, intensity, and timing of exposure. Exposure misclassification is a major concern, because it can bias the estimate of the effect of exposures as well as the estimate of the joint genotype--exposure effect (Rothman et al. 1999). New methods such as biomonitoring approaches (Rothman et al. 1995) and geographic information systems (Kulldorff et al. 1997; Rushton and Lolonis 1996; Ward et al. 2000) can be used to achieve more precise exposure assessments.
Candidate gene selection. The selection of candidate genes is one of the first methodologic issues encountered. Generally, one can investigate the role of a gene whose product is hypothesized to be involved in the biotransformation, cell signal transduction, repair, or disease process relevant to a specific exposure. Sources of toxicologic or other biomedical data that can be used to identify candidate genes include previously published literature (PubMed), the Agency for Toxic Substances and Disease Registry's Toxicological Profiles, the National Library of Medicine's ToxNet, the National Institute for Occupational Safety and Health's Registry of Toxic Effects of Chemical Substances, the National Toxicology Program Report on Carcinogens, On-line Mendelian Inheritance in Man (OMIM), and the Human Genome Epidemiology (HUGE) Net database (see Appendix 2 for website addresses).
Once candidate genes have been selected, sources of genetic information can be used to identify important polymorphisms in candidate gene(s). These sources include websites for specific gene families (e.g., CYPs, NATs), OMIM, the NIEHS's EGP Database, the National Cancer Institute's Cancer Genome Anatomy Project, and polymorphism databases (e.g., the SNPs consortium and the National Center for Biotechnology Information's dbSNPs database) (see Appendix 2 for a listing of relevant URLs). Focusing on polymorphisms with known functional effects is, of course, advantageous.
Efforts to study complex gene-environment interactions are tempered by the difficulty in obtaining adequate sample size (Rothman et al. 2001). Two primary factors to consider are the prevalence of the polymorphism in the population and the magnitude of effect modification. As Caporaso (1999) has pointed out, there is a trade-off between the prevalence of a polymorphism and the magnitude of effect that may be detected. On one hand, common polymorphic variants are less likely to exhibit a strong effect; on the other hand, there is more statistical power in studying these variants because they are more common. Furthermore, the population-attributable risk of common variants will be greater, even if the penetrance is modest.
More recently, investigators have expanded their study design to include analysis of haplotypes. Haplotype analysis is advantageous in that more information about variation in a gene is captured by this approach relative to single polymorphisms, and thus studies using haplotypes should aid in elucidating the role of genetic variation in complex disease (Nebert 2002). Inferring haplotypes from genotype data requires using specific algorithms (e.g., Terwilliger and Ott 1994), and methods are evolving to include adjustment for covariates in the analysis (Schaid et al. 2002).
Selection of a method to obtain samples for genotyping. Collection of DNA samples from the study population is an area of technologic evolution. Besides venous blood samples, from which DNA can be extracted, buccal cell collection brushes (Walker et al. 1999) or mouth washes (Garcia-Closas et al. 2001; Heath et al. 2001) have been employed and offer increased convenience to the study participant, but DNA yield can be substantially lower.
Informed consent. Informed consent for genetic testing is also an important consideration. Beskow et al. (2001) recently described the major issues to consider in obtaining informed consent and developed a general template for researchers to use (see also CDC 2002). In addition, the Department of Health and Human Services (DHHS) provides information about human subjects protection, and templates for informed consent protocols can be accessed at the DHHS website (Appendix 2).
Selection of a genotyping method. Many different methods can be used to genotype subjects. Choosing an appropriate method and using quality control procedures are critical because even minor genotype misclassification can substantially bias study results (Garcia-Closas et al. 1999; Rothman et al. 1999). The choice of method depends on both the type of polymorphism to be analyzed and the type of sample obtained. DNA sequence analysis is considered the gold standard, but it is time-consuming and expensive. Restriction fragment length polymorphism analysis can be used if the polymorphism of interest is known to result in the addition or deletion of a restriction site. More recent, high-throughput approaches include 5'-nuclease-based fluorescence assays (Taqman), matrix-assisted laser desorption/ionization-time-of-flight (MALDI-TOF) mass spectrometry analysis, and DNA microarrays (Shi 2001).
Data analysis. Botto and Khoury (2001) have advocated that, in the context of a case-control study where exposure and genotype are dichotomized, the conventional 2 x 2 table analysis of exposure and disease be expanded to include genotype, yielding a 2 x 4 table. In this manner, the raw exposure and genotype data are displayed in such a way that relative risk estimates for each factor alone and their joint effect can be easily generated. Attributable fractions also can be computed from these data. Regression models of interactions can also be employed (Breslow and Day 1980; Neter et al. 1996). Although not discussed here, issues regarding multiple comparisons and false-positive findings are also important to consider, and readers are referred to De Roos et al. (In press) for guidance.
The role of polymorphisms as determinants of health is being explored in many areas of public health research. In environmental health, recently gathered epidemiologic and toxicologic data suggest that the health effects of many different types of exposures can be modified by polymorphisms, although the effect modification may be weak and the power of many studies is inadequate to demonstrate an effect. Current and future efforts to identify new polymorphisms in genes involved in environmental response will broaden the scope of potential genetic effect modifiers. Determining the effect of these polymorphisms (phenotype) will then be of paramount importance.
Although the individual risk associated with a polymorphism may be relatively low, the population-attributable risk may be large, and thus this area of research merits investigation. As newly identified and previously known polymorphisms are incorporated into epidemiologic research, gene-environment interactions can be detected and quantified. Through toxicologic studies, the mechanisms of these interactions can be elucidated. Correlations between biomarkers of exposure and effect with disease outcomes will facilitate the process of identification of variants that act as effect modifiers. As with any scientific endeavor, intriguing results in this area of research need to be replicated in different studies and populations to confirm the role of a variant as an effect modifier.
Although many gene-environment interaction studies on human populations have been completed in the past decade, the number of examples demonstrating important and consistent positive relationships is remarkably small. It now appears that the "one gene, one risk factor" approach to understanding the etiology of environmentally related chronic diseases is not likely to yield high rewards. Nevertheless, it remains clear that most chronic diseases of public health importance arise from a complex and often poorly understood combination of genetic and environmental factors. New tools for high throughput genotyping of hundreds or thousands of sequence variants in a sample, coupled with very large-scale population-based studies that use sensitive biomarkers and comprehensive exposure assessment strategies are likely to be needed to begin to unravel the complex multiple gene-environment interactions responsible for most chronic diseases of public health importance. This will require new paradigms for interdisciplinary collaborative research that involve very large-scale studies as well as new bioinformatics tools to help scientists make sense of the dizzying array of complex data that will come from such studies. Finally, increasing interest and discussion have been generated about the development of an integrated database that links new findings on exposures, etiologic pathways, relevant genes, polymorphisms in these genes, and their function (De Roos. In press). This database would guide the design of new studies as well as data analysis and interpretation of results (De Roos. In press).
In summary, the ability to detect different levels of risk within the population and greater understanding of etiologic mechanisms are the primary benefits of incorporating genetics into the existing environmental health research framework. The insights gained by employing this framework should ultimately allow for the development of new disease prevention strategies. The use of this information in risk assessments may also be a viable area of development. Finally, whether the use of this information in disease prevention efforts targeted to genetically susceptible individuals is acceptable is an ethical question that is beginning to be addressed and necessitates considerable attention in the future.
Appendix 1. Genes and Polymorphisms with Relevance to Environmental Health Gene Gene product Polymorphism CYP1A1 Aryl hydrocarbon T3801C (m1) hydroxylase A2455G (m2) CYP1A2 Arylamine hydroxylase C-164A CYP2E1 Ethanol-inducible P450 5' flanking repeat region CYP3A4 Steroid-inducible P450 5' promoter A [right arrow]G mutation AHR Aryl hydrocarbon G1721A receptor EPHX1 Epoxide hydrolase Tyr113His His139Arg NQ01 NAD(P)H: quinone oxido- C609T reductase 1 NAT1 N-Acetyltransferase 1 Many alleles NAT2 N-Acetyltransferase 2 Many alleles SULT1A1 Sulfotransferase Arg213His GSTM1 Glutathione S- Deleted (null)allele(s) transferase-[mu] GSTP1 Glutathione S- Ile104Val transferase-[pi] Ala113Val GSTT1 Glutathione S- Deleted (null) allele(s) transferase-[theta] PON1 Paraoxonase Arg192Gln Me155Leu Promoter point mutations VDR Vitamin D receptor RELP in 3' UTR Multiple SNPs HLA-DP [[beta].sub.1] Antigen recognition Lys69Glu protein XPD (ERCC2) Nucleotide excision Lys751Gln repair (NER) enzyme system XPF NER multiple SNPs XRCC1 Base excision repair Arg399Gln APE1 Apurinic/apyrimidinic Asp148Glu endonuclease 1 ALAD [delta]-Aminolevulinic G177C acid dehydratase TLR4 Type I transmembrane A896G protein D299G TNF-[alpha] Cytokine G-308A 1999 Gene Effect of polymorphism References CYP1A1 Unknown Spurr et al. 1987 None Persson et al. 1997 CYP1A2 Decreased inducibility Chida et al. 1999; Sachse et al. 1999 CYP2E1 Increased activity after Hayashi et al. 1991; ethanol exposure Marchand et al. 1999 CYP3A4 Unknown, perhaps expression Rebbeck et al. 1998; levels Walker et al. 1998 AHR CYP1A1 inducibility? Smart and Daly 2000 EPHX1 Altered protein stability? Hassett et al. 1994 NQ01 Altered enzyme induction Moran et al. 1999; Ross et a1.1996 NAT1 Rapid vs. slow acetylation Hein et al. 2000 NAT2 Rapid vs. slow acetylation Hein et al. 2000 SULT1A1 Low activity and low thermal Raftogianis et al. stability 1997 GSTM1 No enzyme produced Seidegard et al. 1988 GSTP1 Altered activity and Ali-Osman et al. substrate affinity 1997 GSTT1 No enzyme produced Pemble et al. 1994; Wiebel et al. 1999 PON1 Change in activity and Furlong et al. 2002; substrate specificity Humbert et al. Change in enzyme expression 1993 levels VDR Unknown Cooper and Umbach 1996 Known for some SNPs HLA-DP [[beta].sub.1] Change in CD4+ recognition Richeldi et al. 1993 XPD (ERCC2) Improved function Dybdahl et al. 1999 XPF Unknown Fan et al. 1999 XRCC1 Unknown Shen et al. 1998 APE1 Reduced endonuclease activity Hadi et al. 2000 ALAD Alleles 1 and 2, 2 allele Wetmur 1994 yields a more electronega- tive protein TLR4 Unknown Arbour et al. 2000 Altered cell signal transduc- tion after LPS exposure TNF-[alpha] Altered transcriptional Abraham and Kroeger regulation? 1999 Abbreviations: RFLP, restriction-fragment-length polynorphism; UTR, untranslated region.
Appendix 2. Websites
Environmental health websites
Agency for Toxic Substances and Disease Registry's Toxicological Profiles
National Library of Medicine's ToxNet
National Institute of Environmental Health Sciences Environmental Genome Project
National Toxicology Program Report on Carcinogens
National Institute for Occupational Safety and Health (NIOSH), Registry of Toxic
Effects of Chemical Substances (RTECS)
Genetic information websites
On-line Mendelian Inheritance in Man (OMIM)
Human Genome Epidemiology (HuGE) Net
Cancer Genome Anatomy Project (CGAP)
The Pharmacogenetics and Pharmacogenomics Knowledge Database
http://www.pharmgkb.org/do/serve?id = home.welcome
National Center for Biotechnology Information (NCBI) dbSNPs
Centers for Disease Control and Prevention (CDC)
Department of Health and Human Services (DHHS)
University of Washington Center for Ecogenetics and Environmental Health
University of Cincinnati Center for Environmental Genetics
University of Washington Institute for Public Health Genetics
University of Michigan Public Health Genetics Interdepartmental Concentration
Table 1. Proposed genetic effect modifiers of common exposures. Exposure Outcome Gene Arsenic Arsenic metabolites in GSTM1 urine GSTT1 Methyltransferase Beryllium Chronic beryllium disease HLA-DP[[beta].sub.1] Lead Blood lead level ALAD Bone lead level ALAD VDR Mercury Atypical porphyrin CPOX profiles UROD Alcohol Esophageal cancer ALDH2 Aflatoxin [B.sub.1] Aflatoxin-albumin adducts CYP1A2 CYP3A4 HCC GSTM1 EPHX1 Heterocyclic amines Colon cancer NAT2 Breast cancer NAT2 SULT1A1 Aromatic amines Bladder cancer NAT2 (dye industry) Halomethanes Metabolite levels in GSTT1 blood Benzene Hematotoxicity CYP2E1 NQ01 Sister chromatid exchange GSTT1 in lymphocytes Halogenated solvents Renal cell carcinoma GSTT1 (e.g., TCE) Organochlorine Immunotoxicity CYP1A1 compounds (e.g., CYP1A2 PCBs, TCDD) AHR Organophosphate Chromosomal aberrations PON1 pesticides GSTM1 GSTT1 CYP3A4 Butadiene Sister chromatid exchange GSTT1 in lymphocytes Lipopolysaccharide FE[V.sub.1] TLR4 (endotoxin) Hay dust TNF-[alpha] production in TNF[alpha] hypersensitivity pneumonitis Ozone Influx of inflammatory TLR4 cells in the lung Airborne PAHs PAH metabolites in urine, CYP1A1 DNA adducts, or GSTM1 measures of NAT2 genotoxicity GSTP1 EPHX1 Lung cancer GSTM1 Nitro-PAHs Genotoxic effects in NAT2 respiratory tract Ultraviolet light Basal cell carcinoma XPD Ionizing radiation DNA damage in lymphocytes XPD XPF XRCC1 Prolonged cell cycle APE1 delay Tobacco smoke Lung cancer CYP1A1 GSTM1 NAT1 NAT2 EPHX1 XRCC1 Bladder cancer CYP1A2 NAT2 GSTM1 Bronchogenic carcinoma AHR Emphysema and chronic EPHX1 obstructive pulmonary GSTM1 disease Environmental Lung cancer GSTM1 tobacco smoke Exposure Rating (a) Reference Arsenic 3 Chiou et al. 1997; Vahter 2000 3 3 Beryllium 1 Richeldi et al. 1993; Richeldi et al. 1997; Saltini et al. 1998 Lead 1 Kelada et al. 2001; Schwartz et al. 1995; Wetmur 1994 1 Fleming et al. 1998; Schwartz et al. 1997 2 Schwartz et al. 2000a, 2000b Mercury 3 Grandchamp et al. 1995; Rosipal et al. 1999 3 Mendez et al. 1998; Moran-Jimenez et al. 1996 Alcohol 1 Chao et al. 2000; Hori et al. 1997; Tanabe et al. 1999; Yokoyama et al. 1996, 1999 Aflatoxin [B.sub.1] 3 Eaton et al. 1995 3 Gallagher et al. 1996 2 London et al. 1995; McGlynn et al. 1995 2 Heterocyclic amines 2 Brockton et al. 2000; Gil and Lechner 1998; Hein et al. 2000; Lang et al. 1986 2 Deitz et al. 2000 2 Zheng et al. 2001 Aromatic amines 1 Cartwright et al. 1982; Hanke and (dye industry) Krajewska 1990 Halomethanes 3 Landi S et el. 1999; Pegram et al. 1997 Benzene 2 Ross et al. 1996; Rothman et al. 1997 2 2 Xu et al. 1998 Halogenated solvents 2 Bruning et al. 1997; Sweeney et al. (e.g., TCE) 2000 Organochlorine 3 Nebert et al. 1996 compounds (e.g., 3 Landi MT et al. 1999; Stresser and PCBs, TCDD) Kupfer 1998 3 Nebert et al. 1996 Organophosphate 2 Au et al. 1999 pesticides 2 2 3 Eaton 2000; Sams et al. 2000 Butadiene 2 Kelsey et al. 1995; Norppa et al. 1995; Wiencke et al. 1995 Lipopolysaccharide 2 Arbour et al. 2000 (endotoxin) Hay dust 2 Schaaf et al. 2001 Ozone 3 Kleeberger et al. 2000 Airborne PAHs 2 Binkova et al. 1996; Knudsen et al. 1999; 2 Merlo et al. 1998; Motykiewicz et al. 1998; 2 Nielsen et al. 1996; Viezzer et al. 1999; 2 Whyatt et al. 2000; Wu et al. 1998 2 2 Lan et al. 2000 Nitro-PAHs 3 Adamiak et al. 1999; Watanabe et al. 1997 Ultraviolet light 2 Dybdahl et al. 1999 Ionizing radiation 3 Duell et al. 2000; Fan et al. 1999; Lunn et al. 2000 3 3 2 Hu et al. 2001 Tobacco smoke 2 Bartsch et al. 2000; Houlston 2000; Xu et al. 1996 2 Bartsch et al. 2000; Houlston 1999; McWilliams et al. 1995 2 Hein et al. 2000 2 Bouchardy et al. 1998 2 Benhamou et al. 1998 2 Ratnasinghe et al. 2001 3 Nebert et al. 1996 1 Marcus et al. 2000a, 2000b 2 Engel et al. 2002 3 Nebert et al. 1996 2 Koyama and Geddes 1998 2 Environmental 2 Bennett et al. 1999 tobacco smoke Abbreviations: TCDD, 2,3,7,8-tetrachlorodibenzo-p-dioxin; TCE, tetrachloroethylene; PAHs, polycyclic aromatic hydrocarbons; PCB, polychlorinated biphenyls; TNF, tumor necrosis factor. (a) Rating system: 1, associations with laboratory evidence and supportive epidemiologic data; 2, associations with laboratory evidence and suggestive epidemiologic data; 3, associations proposed from basic scientific laboratory reports.
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Samir N. Kelada, (1) David L. Eaton, (1,2) Sophia S. Wang, (3) Nathaniel R. Rothman, (3) and Muin J. Khoury (4)
(1) Department of Environmental Health, University of Washington School of Public Health and Community Medicine, and (2) Center for Ecogenetics and Environmental Health, University of Washington, Seattle, Washington, USA; (3) Division of Cancer Epidemiology and Genetics, National Cancer Institute, National Institutes of Health, Bethesda, Maryland, USA; (4) Office of Genomics and Disease Prevention, National Center for Environmental Health, Centers for Disease Control and Prevention, Atlanta, Georgia, USA
Address correspondence to D.L. Eaton, Box 354695, Dept. of Environmental Health, University of Washington, 4225 Roosevelt Way NE, Ste. 100, Seattle, WA 98105-6099 USA. Telephone: (206) 685-3785. Fax: (206) 685-4696. E-mail: firstname.lastname@example.org
This work was supported in part by the National Institute of Environmental Health Sciences Center for Ecogenetics and Environmental Health (P30ES07033), the Environmental Toxicology and Pathology training grant (5T3207032), and the CDC Center for Genomics in Public Health (ASPH/CDC/ASTDR grant S1946-21/21), University of Washington.
The authors declare they have no conflict of interest.
Received 17 October 2002; accepted 24 April 2003.
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|Author:||Khoury, Muin J.|
|Publication:||Environmental Health Perspectives|
|Date:||Jun 15, 2003|
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