PMCCPMCCPMCC

Search tips
Search criteria 

Advanced

 
Logo of envhperEnvironmental Health PerspectivesBrowse ArticlesAbout EHPGeneral InformationAuthorsMediaProgramsPartnerships
 
Environ Health Perspect. Aug 2006; 114(8): 1297–1300.
Published online Apr 4, 2006. doi:  10.1289/ehp.8939
PMCID: PMC1552014
Research
Children's Health
PAH–DNA Adducts in Cord Blood and Fetal and Child Development in a Chinese Cohort
Deliang Tang,1,2 Tin-yu Li,3 Jason J. Liu,1 Yu-hui Chen,1 Lirong Qu,1 and Frederica Perera1,2
1 Department of Environmental Health Sciences and
2 Columbia Center for Children’s Environmental Health, Mailman School of Public Health, Columbia University, New York, New York, USA
3 Chongqing Children Hospital, Chongqing, China
Address correspondence to D. Tang, Mailman School of Public Health, Columbia University, Department of Environmental Health Sciences, Columbia University, 701 W. 168th St., Room 509, New York, NY 10032 USA. Telephone: (212) 305-1704. Fax: (212) 305-0596. E-mail: dt14/at/columbia.edu
The authors declare they have no competing financial interests.
Received December 19, 2005; Accepted April 4, 2006.
Polycyclic aromatic hydrocarbons (PAHs) are an important class of toxic pollutants released by fossil fuel combustion. Other pollutants include metals and particulate matter. PAH–DNA adducts, or benzo[a]pyrene (BaP) adducts as their proxy, provide a chemical-specific measure of individual biologically effective doses that have been associated with increased risk of cancer and adverse birth outcomes. In the present study we examined the relationship between prenatal PAH exposure and fetal and child growth and development in Tongliang, China, where a seasonally operated coal-fired power plant was the major pollution source. In a cohort of 150 nonsmoking women and their newborns enrolled between 4 March 2002 and 19 June 2002, BaP–DNA adducts were measured in maternal and umbilical cord blood obtained at delivery. The number of gestational months occurring during the period of power plant operation provided a second, more general measure of exposure to plant emissions, in terms of duration. High PAH–DNA adduct levels (above the median of detectable adduct level) were associated with decreased birth head circumference (p = 0.057) and reduced children’s weight at 18 months, 24 months, and 30 months of age (p < 0.05), after controlling for potential confounders. In addition, in separate models, longer duration of prenatal exposure was associated with reduced birth length (p = 0.033) and reduced children’s height at 18 (p = 0.001), 24 (p < 0.001), and 30 months of age (p < 0.001). The findings suggest that exposure to elevated levels of PAHs, with the Tongliang power plant being a significant source, is associated with reduced fetal and child growth in this population.
Keywords: birth outcome, coal-burning emission, cord blood, fetal and child development, PAH-DNA adducts
In many industrialized regions of the world, excessive exposure to air pollutants threatens the health of the fetus and the young developing child. Evidence suggests that fetuses and children are more sensitive than adults to the toxicity of many environmental air pollutants because of their higher cell proliferation rates, lower immunologic competence, and decreased ability to detoxify carcinogens and to repair DNA damage (Anderson et al. 2000; National Research Council 1993; Perera et al. 2004; World Health Organization 1986).
Polycyclic aromatic hydrocarbons (PAHs) are among the most harmful air pollutants and are generated by the incomplete combustion of fossil fuels such as coal, diesel, and gasoline. PAHs are also present in tobacco smoke and grilled or broiled foods. A number of PAHs, including benzo[a]pyrene (BaP), are known human mutagens and carcinogens. Some PAHs are transplacental carcinogens in experimental bioassays, producing tumors in the liver, lung, lymphatic tissues, and nervous system of the offspring (Bulay and Wattenberg 1971; Rice and Ward 1982; Vesselinovitch et al. 1975). There is growing evidence that PAHs are also developmental toxicants in humans (Dejmek et al. 2000; Perera et al. 1998, 2003, 2004; Wu et al. 2003). Because PAH–DNA adducts reflect individual variation in exposure, absorption, metabolic activation, and DNA repair, they provide an informative individual biologic dosimeter and risk marker.
Currently, the Columbia Center for Children’s Environmental Health is carrying out three parallel studies in Krakow (Poland), New York City (USA), and Tongliang (China) to examine the impact of in utero exposure to airborne PAHs and other combustion-related pollutants on the health and development of newborns (Perera et al. 2005). The present study in Tongliang was carried out in collaboration with the Chongqing University of Medical Sciences and the Desert Research Institute.
The city of Tongliang has a population of approximately 810,000, and the birth rate is at 3–8/1,000. The city is situated in a small basin approximately 3 km in diameter. A coal-fired power plant located south of the town center operated during the dry season from 1 December to 31 May before 2004 to compensate for the insufficient hydraulic power during that time period. This plant was the principal source of local air pollution, because in 1995 nearly all domestic heating and cooking units were converted to natural gas, and motor vehicles are not a major source. The plant was not equipped with modern pollution reduction technology and combusted about 25,000 tons of high-sulfur coal during each annual 6-month period of operation. This report concerns a cohort of newborns whose gestational period overlapped with the months of power plant operation from 1 December 2001 to 31 May 2002.
As reported previously, the air monitoring data collected as part of this study indicate that Tongliang has a higher PAH level than does Krakow or New York City (Chow et al. 2006; Perera et al. 2005). The monitoring data also suggest that marked seasonal variation in air pollution was attributable in large part to power plant emissions (Chow et al. 2006). For example, concentrations of PAHs and particulate matter with aerodynamic diameter ≤ 2.5 μm (PM2.5) were highest during the winter (December–February) and lowest during the summer (June–August). Concentrations of ambient PAHs of relatively high molecular weight (168–266) were 1.5–3.5 times higher during the power plant’s operational period. PAHs in this molecular weight range include BaP and benzo[e]pyrene, which are known byproducts of coal combustion. The air monitoring data thus provide compelling evidence that the power plant was the major contributor to PAHs in air.
We hypothesized that higher PAH biologic effective doses, as measured by higher levels of PAH–DNA adducts in the umbilical cord blood, will lead to worse birth outcomes and affect the physical growth of the children. Our previous study in Krakow showed that mothers and newborns with higher exposure to ambient air pollution had increased PAH–DNA adducts (Whyatt et al. 1998), and that newborns with more PAH–DNA adducts had significantly decreased birth weight, birth length, and head circumference (Perera et al. 1999). We also hypothesized that longer durations of in utero exposure would be associated with worse outcomes.
The power plant was permanently shut down in May 2004 after the Tongliang County government determined that its shutdown would significantly improve local health and have minimal adverse social and economic impacts. After the shutdown, we enrolled a second cohort of mothers and newborns to compare the health of children with and without in utero exposure to the emissions of the power plant. The data collected from that cohort will appear in future publications. Because coal-fired power plants currently produce 75% of China’s electricity and most new plants are being built to burn coal, results from the Tongliang study have implications for the health of many other children in China.
Study subjects
The subjects are 150 children born to nonsmoking Chinese women who gave birth at the Tongliang County Hospital, Tongliang Traditional Chinese Medicine Hospital, Tongliang Maternal Children Health Hospital, and Bachuan Hospital between 4 March 2002 and 19 June 2002. The women were selected using a screening questionnaire when they checked in for delivery. Eligibility criteria included current non-smoking status, ≥ 20 years of age, and residence within 2.5 km of the Tongliang power plant. We recruited every eligible woman who gave birth at one of the four hospitals between 4 March 2002 and 19 June 2002. Their demographic characteristics are presented in Table 1. All eligible women agreed to enter the study, with 10.6% (16 of 150) lost to follow-up through their children’s age of 30 months. All subjects gave informed written consent by completing a form approved by the Columbia University Institutional Review Board and Chongqing University of Medical Sciences.
Table 1
Table 1
Demographic characteristics of the population (n = 150).
Personal interview
A 45-min questionnaire was administered by a trained interviewer after delivery. The questionnaire elicited demographic information, lifetime residential history (location of birth and duration of residence), history of active and passive smoking (including number of household members who smoke), occupational exposure, medication information, alcohol use during each trimester of pregnancy, and consumption of PAH-containing meat (frequency of eating fried, broiled, or barbecued meat during the last 2 weeks). Socioeconomic information related to income and education was also collected.
Biologic sample collection and analysis
Maternal blood (10 mL) was collected within 1 day postpartum, and umbilical cord blood (40–60 mL) was collected at delivery. Samples were transported to the field laboratory at the Tongliang County Hospital immediately after collection. All samples were processed there. For blood samples, the buffy coat, packed red blood cells, and plasma were separated and stored at −70°C.
DNA adducts
We analyzed BaP–DNA adducts in extracted white blood cell (WBC) DNA using the modified high-performance liquid chromatography–fluorescence method (Alexandrov et al. 1992), which detects BaP tetrols. This assay is a sensitive and specific method for measuring BaP–DNA adducts in WBCs from individuals exposed to BaP (Bartsch and Hietanen 1996) and has a 12% coefficient of variation (Perera et al. 2005). Among 150 blood samples, 19 of them did not have enough DNA for the assay. Of the remaining 131 samples, 104 had detectable adduct levels, and 27 had nondetectable adduct levels. We assigned a value of 0.125, which is half of the adduct detection limit of 0.25, to the nondetectable samples. Samples were run coded, and samples from mother–child pairs were run in the same batch to minimize batch effects.
Measures relevant to birth outcomes and physical development
Birth weight, birth length, and head circumference were measured immediately after parturition. Information abstracted by the research workers from mothers’ and infants’ medical records after delivery included date of delivery; gestational age at birth (based on the last menstrual period); infant sex, birth weight, length, head circumference, and malformations; maternal height, prepregnancy weight, and total weight gain; complications of pregnancy and delivery; and medications used during pregnancy. After the newborns reached 18 months of age, their weight, height, and head circumference were periodically measured at 6-month intervals as indicators of physical development.
Duration of exposure
The estimated duration of in utero exposure to power plant operation was based on the number of months of pregnancy that overlapped with the period of plant operation (1 December 2001 to 31 May 2002). All births occurred between 4 March 2002 and 19 June 2002. Thus, the duration of prenatal exposure to power plant emissions ranged from 3.13 to 6 months for individual children.
Statistical analysis
Measures of PAH–DNA adducts and birth outcomes including birth weight, birth length, and head circumference were log-transformed to normalize the distribution and stabilize the variance. The paired Student’s t-test was used to compare the maternal and cord blood adduct levels. In testing associations with health outcomes, cord blood adducts were used as the independent variable as in prior studies (Perera et al. 1998, 2004). We used multiple linear regression to analyze the association between PAH–DNA adduct level and either birth outcomes or child development, adjusting for potential confounders. Environmental tobacco smoke (ETS), sex, maternal height, and maternal weight were associated with one or more outcomes (p < 0.1) and were considered to be potential confounders of the association between PAH–DNA adducts and birth outcomes and children’s physical growth. Dietary PAH was not included as a covariate because it did not significantly contribute to the final models. High adducts were defined as greater than the median of the detectable adduct value, or 0.36 adducts/10−8 nucleotides.
Outcomes analyzed in this study included birth weight, length, and head circumference, as well as child weight, length, and head circumference at 18, 24, and 30 months of age. Gestational age was found to be a significant predictor of birth outcomes and was therefore added to the models involving birth outcome analysis. In all analyses involving head circumference, maternal head circumference and cesarean status were also considered as covariates. Because analyses of physical development involved repeated measurements, we used linear mixed models with random subject effect to account for the within-subject correlation (Littell 1996).
The demographic characteristics of the 150 mother–newborn pairs from this cohort study are shown in Table 1. The mean cord blood adduct level (0.33 ± 0.14 adducts/108 nucleotides) was somewhat higher than the maternal adduct level (0.29 ± 0.13 adducts/108 nucleotides). Although the difference was not significant, given the estimated 10-fold lower dose to the fetus compared with the mother, the comparable levels of adducts provide evidence that human fetuses are more susceptible than adults to the genotoxic effects of PAHs (Perera et al. 2005).
High cord blood adduct level was significantly associated with decreased birth head circumference (p = 0.057) and reduced infant/child weight at 18 months (p = 0.03), 24 months (p = 0.027), and 30 months of age (p = 0.049) (see Table 2). However, maternal adduct level was neither significantly correlated with cord blood adduct level (r = 0.140, p = 0.299) nor significantly associated with fetal and child growth.
Table 2
Table 2
Association between cord blood PAH–DNA adducts (dichotomized high/low) and birth outcomes/physical growth.a
The interaction term between sex and cord blood PAH–DNA adduct level was not significant, suggesting that the strength of association between adduct level and fetal and child growth was not significantly different between females and males. Because higher power is required to detect significance in the interaction term, the lack of significance of the sex × adduct interaction term was likely due to the lower power from the study’s small sample size. However, significant associations between higher cord blood adduct level and either adverse birth outcome or worse physical development were found only among female infants. Among females, high cord blood adduct level was significantly associated with smaller birth head circumference (p = 0.022), as well as lower weight at 18 months (p = 0.014), 24 months (p = 0.012), and 30 months of age (p = 0.033) and shorter length at 18 months of age (p = 0.033). Among male infants, the corresponding associations were inverse but not significant.
There was a significant association between longer duration of exposure and shorter length at birth (p = 0.032) and height at 18 months (p = 0.001), 24 months (p < 0.001), and 30 months of age (p < 0.001) (Table 3). Among females, longer duration of exposure was significantly associated with shorter length at 18 months (p = 0.024), 24 months (p = 0.018), and 30 months (p = 0.019), whereas among males, longer duration of exposure was also significantly associated with shorter length at 18 months (p = 0.019), 24 months (p = 0.003), and 30 months (p = 0.001).
Table 3
Table 3
Association between duration of exposure and birth outcomes/physical growth.a
In the mixed model evaluating repeat measures of physical growth from birth through age 30 months, high cord blood adduct level was significantly associated with lower weight (p = 0.023) and with smaller head circumference (p = 0.056) in childhood. Duration of exposure was significantly associated with shorter length (p = 0.0001).
We evaluated the association between distance from the power plant and cord adduct level as well as the association between distance and birth outcomes and physical development. Cord adduct level was negatively but not significantly correlated with distance (r = −0.115, p = 0.190). Longer distance from the power plant was significantly associated with greater birth length (p = 0.03), but consistently positive associations between distance and birth outcomes and physical development were not found. Therefore, our analyses indicate that distance is not a good predictor of PAH exposure.
This study examined the associations between cord blood PAH–DNA adducts and birth outcomes and physical growth in a Chinese population exposed to coal-burning emissions. There was a significant association between elevated cord blood adducts and reduced birth head circumference, and with reduced physical growth (decreased weight at 18, 24, and 30 months of age), after adjusting for potential confounders. These are potentially important findings because several previous studies have reported a correlation between reduced fetal growth and poorer cognitive outcomes (Chaikind and Corman 1991; Desch et al. 1990; Matte et al. 2001). The findings are also consistent with prior reports that PAH–DNA cord blood adducts in Caucasian, African-American, and Dominican newborns were significantly associated with reduced fetal growth, alone or in combination with ETS exposure (Perera et al. 1998, 2003).
As noted above, distance from the power plant was not a good predictor of PAH exposure or of outcomes. The present analysis did not include dispersion modeling to take into account meteorologic factors such as wind speed and wind direction. Because of these factors, subjects who live the same distance from the power plant may receive different levels of plant emission exposure, depending on their residential coordinate relative to the plant. This may account for the observation that the distance measurement alone was not a good predictor of adduct level or birth outcomes and physical development. Future analyses will use dispersion modeling to account for the impact of meteorologic factors.
Fetal toxicity from PAHs may be caused by antiestrogenic effects (Bui et al. 1986), binding of constituents to the human aryl hydrocarbon receptor to induce P450 enzymes (Manchester et al. 1987), DNA damage resulting in activation of apoptotic pathways (Meyn 1995; Nicol et al. 1995; Wood and Youle 1995), binding to receptors for placental growth factors resulting in decreased exchange of oxygen and nutrients, or direct effects of carbon monoxide (Dejmek et al. 2000; National Research Council 1986).
In the multiple linear regression analysis, we found that the association between greater adduct level and decreased at-birth head circumference and physical development was significant only among females. In males, there was an inverse relationship between cord blood adduct level and birth outcome/physical development, but the associations were not significant. Although our small sample size provided insufficient power to detect significance in the interaction term, the findings suggest that female fetuses may be more susceptible to the toxicity of PAHs than male fetuses. The mechanism for a possible sex difference is not clear; however, sexual dimorphism of P450 gene expression may lead to higher susceptibility of female fetuses to the toxicity of PAHs compared with male fetuses. CYP1A1 and CYP1B1 are responsible for bioactivating PAHs such that they covalently bind to DNA to form harmful PAH–DNA adducts (Nebert et al. 2004). According to Finnstrom et al. (2002), the expression of CYP1B1 is significantly higher in leukocytes of women than men, and Lin et al. (2003) showed that CYP1A1 and CYP1B1 levels in noninduced lymphocytes were significantly higher in female nonsmokers than in male nonsmokers. In summary, higher levels of CYP1 have been found in females in various studies, whether in the noninduced state or after induction by a chemical compound, which may result in sex differences in susceptibility to the toxic effects of PAHs and other combustion-related pollutants (Finnstrom et al. 2002; Iba et al. 1999; Lin et al. 2003; Oropeza-Hernandez et al. 2003). Our small sample size provided insufficient power to detect significance in the interaction term for sex as an effect modifier of the association between adduct level and birth outcomes and physical development. Future studies with larger samples are needed to determine whether sex is a significant effect modifier of the association between adduct level and birth outcomes and physical development.
Maternal adduct level was neither significantly correlated with cord blood adduct level nor significantly associated with fetal and child growth. This suggests that the biologic dose received by the fetus, which depends partly on its genetic profile, is more relevant than the maternal dose to fetal and child growth. Maternal adduct level may not correlate with the cord blood adduct level because of the different genetic profiles of the mother and the child. Our previous study involving Polish mothers and newborns found that CYP1A1 polymorphisms were not associated with maternal adduct level but were associated with umbilical WBC adduct level (Whyatt et al. 1998).
We also found that fetal and child growth were affected differently by PAH–DNA adduct level and duration of exposure. Higher adduct level was significantly associated with decreased birth head circumference and reduced weight at 18, 24, and 30 months of age, whereas longer duration of exposure was associated with reduced birth length and shorter height at 18, 24, and 30 months of age. In addition, although significant associations between adduct level and fetal and child growth were only found among females, significant associations between duration of exposure and fetal and child growth were present among both males and females. A possible explanation of why longer duration of exposure is significantly associated with worse growth outcomes in both sexes, not just among females, is that although adducts represent the amount of exposure to BaP, duration of exposure represents the amount of exposure to multiple harmful compounds released by the power plant, including other PAHs, PM, and metals. As mentioned above, we were able to attribute seasonal variation in air pollution largely to power plant emissions, which supports the assumption that a longer period of overlap between gestation and plant operation is a proxy for higher in utero exposure to ambient PAHs and PM2.5 and other coal-burning emissions.
This study has the advantage of being based on individual data as well as medical record and questionnaire data. In addition, we were able to quantitatively measure the individual biologically effective dose of BaP through the measurement of BaP–DNA adducts. However, the study was limited by the modest number of subjects (150) for whom data from all relevant domains were available. Because most study subjects were exposed to power plant emission in both the second and third trimesters, we could not evaluate trimester-specific effects of exposure on fetal and child growth. Another limitation was that children received postnatal exposure to power plant emission in addition to prenatal exposure. Because of the power needs of the Tongliang community, the power plant was shut down later than anticipated, and subjects continued to receive exposure to the plant emission after birth. It is therefore not possible to separate the impact of postnatal exposure from that of prenatal exposure on child physical development.
Results from phase 2 of the Tongliang project, which is studying a second cohort of children who were conceived after the power plant shutdown and did not have in utero exposure to power plant emissions, will be presented in future publications.
In conclusion, these results indicate that PAHs from coal-burning power plants are harmful to the developing fetus and child and have implications for energy policy and health. The Tongliang coal-burning power plant was shut down without serious economic consequences to the city, and the energy needs formerly met by the plant were subsequently provided by power from the grid. Because coal-fired power plants currently produce 75% of China’s electricity and most new plants are being built to burn coal, results from the Tongliang study have implications for the health of many other children in China.
Footnotes
This project was supported by the V. Kann Rasmussen Foundation, the National Institute of Environmental Health Sciences (grants 5 P01 ES009600, 5 R01 ES008977, 5 R01ES11158, 5 R01 ES012468, 5 R01 ES10165), the U.S. Environmental Protection Agency (grants R827027, 82860901, RD-832141), and the New York Community Trust.
  • Alexandrov K, Rojas M, Geneste O, Castegnaro M, Camus AM, Pesruzzelli S, et al. An improved fluorometric assay for dosimetry of benzo(a)pyrene diol-epoxide-DNA adducts in smokers’ lung: comparisons with total bulky adducts and aryl hydrocarbon hydroxylase activity. Cancer Res. 1992;52:6248–6253. [PubMed]
  • Anderson LM, Diwan BA, Fear NT, Roman E. Critical windows of exposure for children’s health: cancer in human epidemiological studies and neoplasms in experimental animal models. Environ Health Perspect. 2000;108:573–594. [PMC free article] [PubMed]
  • Bartsch H, Hietanen E. The role of individual susceptibility in cancer burden related to environmental exposure. Environ Health Perspect. 1996;104:569–577. [PMC free article] [PubMed]
  • Bui QQ, Tran MB, West WL. A comparative study of the reproductive effects of methadone and benzo(a)pyrene in the pregnant and pseudopregnant rat. Toxicology. 1986;42:195–204. [PubMed]
  • Bulay OM, Wattenberg LW. Carcinogenic effects of polycyclic hydrocarbon carcinogens administrated to mice during pregnancy on the progeny. J Natl Cancer Inst. 1971;46:397–402. [PubMed]
  • Chaikind S, Corman H. The impact of low birthweight on special education costs. J Health Econ. 1991;10:291–311. [PubMed]
  • Chow J, Watson J, Chen L-W, Koracin D, Zielenska B, Tang D, et al. Exposure to PM2.5 and PAHs from the Tong Liang, China, Epidemiological Study. J Environ Sci Health A Tox Hazard Subst Environ Eng. 2006;41:517–542. [PubMed]
  • Dejmek J, Solansky I, Beneš I, Leníèek J, Šrám RJ. The impact of polycyclic aromatic hydrocarbons and fine particles on pregnancy outcome. Environ Health Perspect. 2000;108:1159–1164. [PMC free article] [PubMed]
  • Desch LW, Anderson SK, Snow JH. Relationship of head circumference to measures of school performance. Clin Pediatr (Phila) 1990;29:389–392. [PubMed]
  • Finnstrom N, Ask B, Dahl ML, Gadd M, Rane A. Intra-individual variation and sex differences in gene expression of cytochromes P450 in circulating leukocytes. Pharmacogenomics J. 2002;2(2):111–116. [PubMed]
  • Iba MM, Fung J, Thomas PE, Park Y. Constitutive and induced expression by pyridine and beta-naphthoflavone of rat CYP1A is sexually dimorphic. Arch Toxicol. 1999;73(4–5):208–216. [PubMed]
  • Lin P, Hu SW, Chang TH. Correlation between gene expression of aryl hydrocarbon receptor (AhR), hydrocarbon receptor nuclear translocator (Arnt), cytochromes P4501A1 (CYP1A1) and 1B1 (CYP1B1), and inducibility of CYP1A1 and CYP1B1 in human lymphocytes. Toxicol Sci. 2003;71(1):20–26. [PubMed]
  • Littell RC. 1996. SAS system for mixed models. In: Statistics (Littell RC, Milliken GA, Stroup WW, Wolfinger RD, eds). Cary, NC:SAS Institute Inc., 423–460.
  • Manchester DK, Gordon SK, Golas CL, Roberts EA, Okey AB. Ah receptor in human placenta: stabilization by molybdate and characterization of binding of 2,3,7,8-tetra-chlorodibenzo-p-dioxin, 3-methylcholanthrene, and benzo(a)pyrene. Cancer Res. 1987;47:4861–4868. [PubMed]
  • Matte TD, Bresnahan M, Begg MD, Susser E. Influence of variation in birth weight within normal range and within sibships on IQ at age 7 years: cohort study. BMJ. 2001;323:310–314. [PMC free article] [PubMed]
  • Meyn MS. Ataxia-telangiectasia and cellular responses to DNA damage. Cancer Res. 1995;55:5991–6001. [PubMed]
  • National Research Council 1986. Environmental Tobacco Smoke: Measuring Exposures and Assessing Health Effects. Washington, DC:National Academy Press.
  • National Research Council 1993. Issues in Risk Assessment. Washington, DC:National Academy Press.
  • Nebert DW, Dalton TP, Okey AB, Gonzalez FJ. Role of aryl hydrocarbon receptor-mediated induction of the CYP1 enzymes in environmental toxicity and cancer. J Biol Chem. 2004;279(23):23847–23850. [PubMed]
  • Nicol CJ, Harrison ML, Laposa RR, Gimelshtein IL, Wells PG. A teratologic suppressor role for p53 in benzo[a]pyrene-treated transgenic p53-deficient mice. Nat Genet. 1995;10:181–187. [PubMed]
  • Oropeza-Hernandez LF, Lopez-Romero R, Albores A. Hepatic CYP1A, 2B, 2C, 2E and 3A regulation by methoxychlor in male and female rats. Toxicol Lett. 2003;144(1):93–103. [PubMed]
  • Perera FP, Jedrychowski W, Rauh V, Whyatt RM. Molecular epidemiologic research on the effects of environmental pollutants on the fetus. Environ Health Perspect. 1999;107:451–460. [PMC free article] [PubMed]
  • Perera FP, Rauh V, Tsai WY, Kinney P, Camann D, Barr D, et al. Effects of transplacental exposure to environmental pollutants on birth outcomes in a multi-ethnic population. Environ Health Perspect. 2003;111:201–205. [PMC free article] [PubMed]
  • Perera FP, Tang D, Jedrychowski W, Hemminki K, Santella RM, Cruz LA, et al. Biomarkers in maternal and newborn blood indicate heightened fetal susceptibility to pro-carcinogenic DNA damage. Environ Health Perspect. 2004;112:1133–1136. [PMC free article] [PubMed]
  • Perera FP, Tang D, Whyatt RM, Lederman S, Jedrychowski W. DNA damage from polycyclic aromatic hydrocarbons (PAHs) measured by benzo[a]pyrene DNA-adducts in mothers and newborns from northern Manhattan, the World Trade Center area, Poland, and China. Cancer Epidemiol Biomarker Prev. 2005;14:709–714.
  • Perera FP, Whyatt RM, Jedrychowski W, Rauh V, Manchester D, Santella RM, et al. Recent developments in molecular epidemiology: a study of the effects of environmental polycylic aromatic hydrocarbons on birth outcomes in Poland. Am J Epidemiol. 1998;147:309–314. [PubMed]
  • Rice JM, Ward JM. Age dependence of susceptibility to carcinogenesis in the nervous system. Ann NY Acad Sci. 1982;381:274–289. [PubMed]
  • Vesselinovitch SC, Kandala DR, Mihailovich N. Neoplastic response of mouse tissues during perinatal age periods and its significance in chemical carcinogenesis. NCI Monogr. 1975;51:230–250.
  • Whyatt RM, Santella RM, Jedrychowski W, Garte SJ, Bell DA, Ottman R, et al. Relationship between ambient air pollution and DNA damage in Polish mothers and newborns. Environ Health Perspect. 1998;106:821–826. [PMC free article] [PubMed]
  • Wood KA, Youle RJ. The role of free radicals and p53 in neuron apoptosis in vivo. J Neurosci. 1995;15:5851–5857. [PubMed]
  • World Health Organization 1986. Principles for Evaluating Health Risks from Chemicals during Infancy and Early Childhood: The Need for a Special Approach. WHO Environmental Health Criteria 59. Geneva:World Health Organization.
  • Wu J, Ramesh A, Nayyar T, Hood DB. Assessment of metabolites and AhR and CYP1A1 mRNA expression subsequent to prenatal exposure to inhaled benzo(a)pyrene. Int J Dev Neurosci. 2003;21:333–346. [PubMed]
Articles from Environmental Health Perspectives are provided here courtesy of
National Institute of Environmental Health Science