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Exposure to naphthalene, an IARC-classified possible carcinogen and polycyclic aromatic hydrocarbon (PAH), is widespread, though resulting health effects are poorly understood. Metabolites of naphthalene, 1- and 2-naphthol, are measurable in urine and are biomarkers of personal exposure. Chromosomal aberrations (CAs), including translocations, are established markers of cancer risk and a bio-dosimeter of clastogenic exposures. Although prenatal (maternal) PAH exposure predicts CAs in cord blood, few studies have examined CAs in school-age children and none has examined their association with metabolites of specific PAHs.
Using Whole Chromosome Paint Fluorescent in Situ Hybridization, we documented CAs including translocations, in 113 five year old urban minority children and examined their association with concurrent concentrations of PAH metabolites measured in urine.
We report that in lymphocytes, the occurrence and frequency of CAs including translocations are associated with levels of urinary 1- and 2-naphthol. When doubling the levels of urinary naphthols, gender-adjusted Odds Ratio (OR) for CAs are 1.63 (95%CI: 1.21, 2.19) and 1.44 (95%CI: 1.02, 2.04) for 1-and 2-naphthol respectively; and for translocations: OR=1.55 (95%CI: 1.11-2.17) and 1.92 (95%CI: 1.20-3.08) for 1- and 2-naphthol respectively.
Our results demonstrate that markers of exposure to naphthalene in children are associated with translocations in a dose related manner, and that naphthalene may be a clastogen.
Indoor exposure to elevated levels of naphthalene is prevalent in large regions of the world. This study is the first to present an association between a marker of naphthalene exposure and a pre-carcinogenic effect in humans.
Naphthalene, the smallest polycyclic aromatic hydrocarbon (PAH) and an IARC possible carcinogen, is ubiquitous in ambient air with high volumes of vehicular traffic(1) and is elevated in indoor air when mothballs or stoves burning biomass fuels are used(2-4). Naphthalene, a two-ring PAH, is derived from petroleum and biofuel products and, like other small PAHs, is found entirely in gas phase rather than as a particulate. Human exposure to naphthalene is primarily through inhalation, though ingestion and dermal absorption can be mayor contributors to exposure in both occupational and non-occupational settings(5-7). Due to the volatile nature of naphthalene, a box of naphthalene-containing mothballs can elevate indoor naphthalene levels to levels compatible with mid to upper level occupational exposure, with higher ambient concentrations in smaller apartments or enclosed areas(2). Some Caribbean immigrant families in New York City (NYC) report using naphthalene containing mothballs as air fresheners (with resulting increased rates of hemolytic anemia)(8). Indoor exposure to naphthalene affects more than half of the world’s population and represents a potentially important environmental contributor to the global burden of disease(3, 4, 7). Understanding potential downstream effects of naphthalene exposure has become increasingly relevant.
Once inhaled or ingested, naphthalene is metabolized by cytochrome P450 enzymes to form naphthalene oxide, which are rearranged to 1- and 2-naphthol. These metabolites are then conjugated with glucuronic acid and sulfate to be excreted in the urine and have been used extensively as biomarkers for exposure(9, 10). Measurements of urinary 1-and 2-naphthol have demonstrated consistently detectable levels in almost all samples analyzed including 100% of NHANES samples tested(11). Urinary levels of 1- and 2-naphthol are markers of occupational(12), vehicular traffic, household(5) and infant mothball exposure(13) and correlate significantly with naphthalene vapor levels in personal air monitors(5, 14).
Urinary metabolites of naphthalene can be useful markers for measuring carcinogenically relevant exposures to naphthalene, as elevated levels of urinary naphthols predict levels of sperm DNA damage(15). Downstream metabolites of 1-naphthol include 1, 4-dihydroxynaphthalene and 1,4-naphthoquinone; while 2-naphthol is metabolized to dihydrodiol and 1,2-naphthoquinone(16) which can also be generated through a 1,2-epoxide intermediate(17). These quinone metabolites have been associated with DNA adducts and marrow stem cell toxicity(8, 13).
Little is known about the direct carcinogenicity of naphthalene; though, there have been reports of laryngeal carcinoma with occupational exposure and colorectal carcinoma in young adults after naphthalene ingestion(18, 19). In occupationally exposed agricultural workers, levels of 2-naphthol in urine predict levels of DNA damage in sperm(15). Increasing levels of DNA strand breakage in lymphocytes correlate with increased air levels of naphthalene(20). Naphthyl-keratin adducts (derived from naphthalene oxide) have been documented in skin of exposed jet fuel workers(21).
Ex vivo exposure of cord blood mononuclear cells to naphthalene and its metabolites has resulted in impaired formation of granulocyte-monocyte colony forming units(22), suggesting potential stem cell susceptibility and oxidative damage with elevated exposure, while exposure to mothballs causes hemolytic anemia in individuals with G6PD deficiency(8, 13). In rodent models using inhalational exposure to naphthalene, dose-dependent cytotoxic effects of naphthalene, mediated by an oxidative mechanism, have been noted in bronchiolar epithelial Clara cells(23), with concentration dependent increases in bronchiolar-alveolar adenomas in mice(24), and olfactory epithelial neuroblastomas in rats(25). In vitro and in vivo work has demonstrated both stable and depurinating glutathione adducts derived from a topical exposure to 1,2-naphthoquinone in mice(23, 26). However there has not been evidence associating naphthalene with clastogenic damage in humans.
Chromosomal aberrations (CAs) are an established marker of cancer risk and are a bio-dosimeter of genotoxic exposures in adults(27). Translocations, the most persistent subtype of CAs, with half-lives of 2-4 years(28, 29) documented after either ionizing radiation or mixed chemical occupational exposures, are considered the most meaningful cytogenetic endpoint for assessing cancer risk(30, 31). In newborns from the Columbia Center for Children’s Environmental Health (CCCEH), an urban birth cohort of underprivileged Dominican and African American children in NYC, we have documented that CAs and translocations in cord blood are associated with prenatal maternal exposure to air polycyclic aromatic hydrocarbons (PAH)(32).
Levels of urinary PAH metabolites in spot urines from a subset of 221 school age CCCEH participants were previously compared with data from NHANES (01-02) and were reported to range 1.6 to 2.5 fold higher for metabolites of naphthalene and 1-hydroxypyrene while levels for metabolites for other fuel derived semi-volatile 3-ring PAHs, phenanthrene and fluorene, were consistent with national data(11, 33).
The objectives of this study were to evaluate 1) whether urinary PAH metabolite measurements predicted occurrence and frequency of CAs and translocations in young school-age children, 2) whether the association between CAs and PAH might differ depending on the family of small ringed PAHs examined, and 3) whether risk of translocations varied with levels of naphthalene metabolites.
The Harlem, Bronx, and Washington Heights- CCCEH- longitudinal birth cohort consists of 697 mother and child pairs followed since pregnancy to examine prenatal effects of air pollutants on health outcomes. Many CCCEH mothers lack a high school diploma (25%), and 45% reported annual household incomes below $10,000 during pregnancy(33). The cohort has 83% retention at age 3 years(34). Children who reached their 5th birthday between February 2005 and December 2007 were entered into an additional study (N=222) that examined predictors of asthma and allergy at age 5 (33). Blood and spot urine samples and PAH-exposure questionnaires querying about the 48 hours prior to the urine collection were collected as previously described (33). We processed an aliquot of fresh blood from those children whose blood and urine samples were collected concurrently after January 2006 (N=113) using Whole Chromosome Paint Fluorescent in situ hybridization (WCP-FISH). All available fresh blood samples that had corresponding spot urine sample measurements were included. All participating mothers signed an approved consent in accordance with the Institutional Review Board of the Columbia University Medical Center. The Centers for Disease Control and Prevention (CDC) laboratory’s role was determined to not constitute engagement in human subjects research.
In the CCCEH laboratory, spot urine samples were aliquotted and frozen (−80°C) prior to shipping to the CDC NCEH Laboratories to be analyzed for PAH metabolites including 1- and 2-naphthol as previously described(11, 33). Enzymatic deconjugation, followed by automated liquid-liquid extraction and quantified by gas chromatography/isotope dilution high-resolution mass spectrometry (GC-IDHRMS) was used for analytical determination of urinary PAH concentrations. To control for differences in urine dilution, specific gravity (SG) was measured using a handheld refractometer as previously described(33).
Aberrations are scored in T-lymphocytes that have a half-life of up to a year invivo. Therefore, detected aberrations should reflect exposures occurring in recent months. At the time of routine follow up visits for 5-year-old CCCEH participants, 0.8 milliliters (mL) of blood was collected in a heparinized tube, and kept at room temperature until processed for WCP-FISH. Fresh samples were cultured and hybridized using the procedures described previously(32). In brief, samples were cultured for 72 hours in PB-Max Complete Media (Invitrogen, Carlsbad, Ca.) at 37°C using standard techniques which preferentially expand T lymphocytes, and including replicate cultures for each sample when possible. We utilized individual WCP (Cytocell, UK) for chromosomes 1, 2, and 4 in red and chromosomes 3, 5, and 6 in green. The colors were chosen in order to facilitate distinguishing individual chromosomes by a combination contrasting colors and morphology. We focused on chromosomes 1-6, which together comprise 39% of the human genome, in order to be comparable with prior work from our group and others (30, 35-38). For each case, chromosomes 1-6 were hybridized on slides using DAPI counter stain (Cytocell, UK). A 6q sub-telomere specific probe (RP11-307K1 and RP11-292F10) was incorporated to assist in differentiating chromosomes 5 and 6.
The 6q sub-telomere specific probe (RP11-307K1 and RP11-292F10) was generated as previously described(32) using Spectrum Red dUTP with a nick translation labeling kit (Vysis, Downer’s Grove, IL). One microliter of the resulting red 6qtel probe was applied to each slide at the time of applying the WCP mixture for chromosomes 1-6 withhybridization and washing as described previously(32). FISH signals were visualized using a luorescence microscope (Olympus Bx-UCB, Olympus, Japan) equipped with appropriate filters (FITC, TRITC, and DAPI) and Cytovision software (Genetix, New Milton, UK).
Scoring was performed by trained clinical cytogenetic technicians who were blinded to identification or exposures of the samples. Inclusion criteria for metaphases to be scored included good spread, absence of broken metaphases, readable color signal intensity and complete visualization of 12 chromosomes and visualization of each centromere. Metaphases containing aneuploidy were not scored for aberrations. All abnormalities found were recorded with their given coordinates and photographed using CytoVision. Questionable aberrations were confirmed using the inverse DAPI feature of CytoVision. All potential CAs were reviewed independently by the principal study cytogeneticist (DW) who also was blinded to exposure and subject identity. Only those approved and classified by DW were entered into the study database.
CAs were classified morphologically and breaks were tabulated according to the PAINT system(30, 39). Only CAs containing clearly visible centromeres were considered “stable” (able to persist in subsequent cell divisions) and were counted in subsequent analyses. Translocations (unbalanced and balanced) were counted as CAs but also were analyzed separately given their recognized advantage for documenting carcinogenically relevant changes(30, 31). For each sample, 750 metaphases (>425 Cell Equivalents, [CE]) were scored and all potential CAs were reviewed. Aberration frequency was calculated per 100CE to be consistent with other cohorts in which WCP FISH is measured(30) and based on the proportion of the genome painted(40). Cells with aneuploidy were not included in those scored for stable aberrations and thus did not go into the calculation of aberration frequency or genome equivalence.
Unidentified red chromosomes were presumed to represent either chromosomes 1, 2, or 4, and unidentified green chromosomes were presumed to be composed of either 3, 5, or 6p. Fragments without centromeres and aneuploidies were not considered stable and were excluded from subsequent analyses.
WCP FISH scoring results were noted by study staff and entered along with chromosome location, slide quadrant and aberration type. The aberration and translocation frequencies were calculated from the number of CAs per number of cells (metaphases) analyzed, adjusted for 100 CE using the correction factors calculated from the proportion of the genome painted simultaneously in a given slide using the formula for two color paints by Lucas(40). Ascribed genetic content was based on the Human Genome Project base-pair (bp) delineation as previously described(32).
Summary statistics were calculated to describe sample characteristics. In order to compare two groups such as those with and without WCP FISH, or the two ethnic groups, Dominicans and African-Americans, we used the T-test or Wilcoxon test for continuous variables and the Chi-square or Fisher’s exact tests for categorical variables. Variables for naphthalene exposure were also compared between the children with and without CAs, and with or without translocations. Spearman correlation coefficient was calculated for describing bi-variate associations between quantitative variables.
CA frequency was defined as number of CAs per 100CE, and translocation frequency as the number of translocations per 100CE(32, 37). Urinary PAH levels had a skewed distribution and were logarithmically transformed in order to meet assumptions for T-tests and to reduce the impact of extreme values when used as the main predictor in the models for presence or frequencies of CA or translocation. Overall exposure variables were created by summing the metabolites derived from each parent PAH as done for analyses with urinary PAH data from NHANES(11). NAPH, the overall exposure variable for naphthalenes, is the sum of 1-and 2-naphthol; for fluorenes, FLUOR is the sum of 2-, 3-, 9-OH fluorene. For pyrene, PYR is 1-OH pyrene as it is the only pyrene metabolite measured. For phenanthrene, PHEN is the sum of 1-, 2-, 3- and 4-OH phenanthrene.
To examine the effect of naphthalene exposure variables, logistic regression models were used for binary outcomes for CAs and translocations (presence vs. absence) and Negative Binomial models were used for the outcome variables of frequencies of CA and translocations. In order to aid in the interpretation of the associations with 1- and 2-naphthol, covariate adjusted odds ratios (OR), along with their confidence intervals, were derived from the parameters in logistic models. Similarly, covariate adjusted mean ratios (MR) of frequencies of CAs and translocations, along with their 95% confidence interval (CI), were derived from the parameters obtained in Negative Binomial models. Because the naphthalene metabolite levels varied between the two ethnic groups in our sample and patterns of exposure to naphthalene might vary by gender, we controlled for ethnicity and child’s sex in the analysis with the whole sample (N=113) and controlled for child’s sex in ethnic group specific analyses. We used the Wald test to detect ethnic group differences in the model parameters documenting the effect of exposure. Statistical significance level of the tests was set at 0.05 and statistical analyses were performed with SAS 9.3.1 and SPSS18.
Of our 221 children with spot urine samples, 113 children had fresh blood samples that met criteria for cytogenetic analysis. These 113 children did not differ in sex, ethnicity, levels of maternal education, or utilization of Medicaid, compared to the 108 children that did not have blood samples processed for WCP-FISH. Children whose blood samples were processed for WCP-FISH were more likely to have been in the presence of a smoker in the 48 hours prior to urine collection. Levels of urinary 1- and 2-naphthol as well as urinary 1-hydroxypyrene (1-OHP) did not differ between the two groups (Table 1).
The 5 year olds have mean frequencies of 0.154 (SD:0.272) for CAs and 0.079 (SD:0.197) for translocations, which is in the reported range for children ages 5-9 (mean 0.15 range 0.07-0.32)(30). However, aberration data on children (after birth) have only been reported for 38 children ages 5-9 and only 7 with >300 CE scored(30).Table 2 includes the characteristics of children with CAs and translocations. In keeping with the PAINT convention(30, 39), translocations included balanced and unbalanced translocations. One translocation had a dicentric chromosome. There did not appear to be clonal rearrangements, nor were there recurring chromosomal rearrangements.
Mothers of African-American (N=47) and Dominican (N=66) participants did not differ in demographic characteristics such as education or eligibility for Medicaid during pregnancy (Table 2). At age five years, African-American children were more likely to live in a home with a smoker, but the two groups did not differ in the proportion of children who were in the presence of a smoker during the 48 hrs prior to the urine collection. Levels of 1-naphthol did not differ by ethnicity, but 2-naphthol levels were significantly higher in Dominicans. Neither CA or translocation frequency, nor the proportion of children with CAs or translocations differed between the two ethnic groups.
Adjustments for dilution were conducted using SG to avoid misclassification reported previously with adjustments using spot creatinine in children with lower muscle mass, pulmonary disease, or using corticosteroids or beta agonist inhalers(33, 41). SG levels ranged from 1.003-1.035 and did not vary with presence or frequency of CAs or translocations.
We examined the ranges of unadjusted urinary metabolite levels from our subgroup of 113 of these five year olds compared to fresh weight (un-adjusted) levels from the youngest members of the 01-02 NHANES cohort (ages 6-11) measured in the same laboratory.
Geometric means of 1- and 2-naphthol were 2871 and 2472ng/L, respectively among African-American children, and 2967 and 4675, respectively in Dominican children.
Among the NHANES cohort geometric means of 1-naphthol was 1430 ng/L (95%CI: 1170, 1730) and 2-naphthol was 1690 ng/L (96%CI: 1560, 1840)(11). Levels of naphthalene metabolites, in particular, 2-naphthol, in these 113 CCCEH children range higher than those of children in NHANES, though when compared with the equivalent ethnic groups in NHANES, our median levels appear in the range of the 75th percentile of NHANES for both Non-Hispanic blacks and Hispanics(11).
Among those factors examined in our study, the only difference noted between children with blood samples collected for analysis by WCP FISH and those whose blood was not processed for FISH was that those collected for FISH were from children that were more likely to be in the presence of a smoker during the 48 hrs prior to their urine collection (Table 1). However, a child’s presence in the company of a smoker during the 48 hrs prior to the urine collection did not predict a child’s 1- and 2-naphthol levels, CA, translocation, or the relationship between naphthol levels and CA (data not shown). As a result, whether or not the child was in the company of a smoker was not used as a control variable. The proportion of smoking at home in 47 African-Americans (36.96%) was higher than in 66 Dominicans (16.67%) (Chi square test p =0.025), however presence of CAs and presence of translocations did not differ between genders or ethnic groups. Consistent with findings in newborns, both presence and frequency of CAs did not differ with exposure to passive smoking(8, 21).
In the 113 children with measurements for both urinary PAH metabolites and CAs, we examined whether levels of urinary PAH metabolites predicted whether a child would have at least one CA (of any type) or a translocation (Table 3). Levels of NAPH and 1- and 2-naphthol differed significantly between children with and without translocations. Levels for NAPH and 1-naphthol differed significantly between children with and without CAs. Urinary metabolite levels for PYR, FLUO and PHEN did not differ with occurrence of either CAs or translocations (Table 3).
Associations between frequencies of CAs and urinary PAH metabolites for our population of 113 five year olds are shown in Table 4. Bivariate correlations between frequencies of CAs and 1- and 2-naphthol as well as the NAPH summed term, stratified by ethnicity suggest an ethnic disparity in the association between CAs and translocations with urinary naphthols. Higher 1-naphthol was associated with higher frequency of CAs though this association was only observed in the Dominican 5 year olds (r=0.387, p<0.01). Translocations were higher with higher levels of NAPH, particularly in Dominican children (r=0.334, p <0.01). There were no recurrent breakpoints among the translocations observed.
Among the study subjects, 35 children had CAs. Of these, 20 children had translocations. Levels of 1- and 2-naphthol did not vary with presence of a smoker in the child’s home, nor did they vary with a child’s reported consumption of smoked meat or charbroiled hamburgers (data not shown). Levels of 2-naphthol (but not 1-naphthol) seemed higher in girls (p= 0.08) and in Dominicans (p=0.01).
To describe the effects of exposures on frequency of CA and translocations, mean ratios (MR) and odds ratios (OR) were derived for a doubling of naphthol levels (Table 5). After adjusting for sex and ethnicity, presence of both CAs and translocations were associated with higher levels of either 1- or 2-naphthol. For all children (combining both genders and ethnicities), a doubling of 1-naphthol was associated with increased odds for having CAs (OR = 1.23; 95%CI: 1.01, 1.48). Similarly, for 2-naphthol, doubling the 2-naphthol levels appeared to associate with non-significantly increased odds for CAs (OR=1.19; 95%CI: 0.90, 1.56). However, when we examined Dominican children separately, the effect was stronger for both 1-naphthol (OR =1.63; 95%CI: 1.21-2.19) and 2-naphthol (OR=1.44; 95%CI: 1.02-2.04).
In contrast, for translocations, the odds of having a translocation were significantly elevated when either 1- or 2-naphthol were higher. The odds for translocations were also significantly associated with higher levels of the sum variable (NAPH) when all children were examined together. However, when examined separately by ethnicity, the odds of having translocations were significantly elevated only among Dominicans. In Dominican children, for a doubling of 2-naphthol levels, the odds of having translocations were significantly increased (OR 1.92; 95%CI: 1.20, 3.08).
When we examined the effect of naphthol on the mean frequencies of CAs, the mean frequency of CAs increased by doubling 1-naphthol (MR: 1.38; 95%CI: 1.10, 1.72) in Dominicans but not in African-Americans. For this doubling, the group difference between the two ethnic groups was significant (p<0.05). In contrast, the association between naphthols and frequency of translocations did not differ by ethnicity.
To examine possible dose-response, levels of 2-naphthol were trichotomoized by tertiles using the lowest one-third as the referent group. After adjusting for gender and ethnicity, Children with 2-naphthol in the highest group (above 5800 ng/L) were significantly more likely to have translocations (OR 4.29; 95% CI: 1.11-16.55) when compared with those in the lowest group (below 2540 ng/L). Similarly, children in the highest group of 2-naphthol exposure also appeared to have a higher frequency of translocations (MR 3.23; 95%CI: 0.85-12.50) (Table 6), though the results were not significant. The effect of increasing naphthol on CAs or translocations was not dominated by any one chromosome, in contrast to our findings in newborns, which were dominated by chromosome 6(32).
Although 2-naphthol is derived exclusively from naphthalene, 1-naphthol can result from metabolism of carbaryl as well as from metabolism of naphthalene. Levels of carbaryl in prenatal air samples from mothers in our population were detectable in only one mother and consequently are not measured in children our cohort(42).To determine the source of 1-naphthol in our samples, we examined the ratio of 1- to 2-naphthol in the urine samples of the 113 participants as described by Meeker et al.(15). Carbaryl was an unlikely contributor in 75% of the children, whose ratio are below the threshold level of 2(15). This proportion is similar to the proportion described among Hispanic pregnant women(15, 43). The proportion with ratios greater than 2 did not differ between those with and without aberrations or between those with and without translocations. The mean ratio of 1- to 2-naphthol also does not differ between those with and without aberrations or between those with and without translocations.
Our results demonstrate that markers of exposure to naphthalene in young children are associated with translocations and stable chromosomal aberrations in lymphocytesin a dose related manner. Childhood is a period of heightened susceptibility when exposure to environmental toxins can result in molecular changes that act as determinants for later disease. Exposures to low levels of common environmental toxins such as naphthalene during key periods of development may increase long-term risk of disease. CAs in lymphocytes are used as a biodosimeter of protracted personal exposure to low dose radiation(37) and of occupational exposure to genotoxins(31). Air levels of PAHs predict chromosomal aberrations in occupationally exposed adults(30). In studies on older children (8-19 years), frequencies of CAs correlate with levels of ambient pollutants(40). Translocations, the most persistent aberrations (half-life: 2-4 years), are a biodosimeter of low dose clastogenic exposures and can persist 10-13 years after exposure(29). WCP-FISH has been used to facilitate documentation of translocations. Previous studies have demonstrated that frequency of translocations increases with age and smoking exposure(30) and that they can persist over years in serially measured occupational cohorts(27-31).
Few studies have used WCP-FISH in peripheral blood to examine effects of environmental exposures in children postnatally. In prior work we have shown that occurrence of stable aberrations is non-random and is not proportional to the genomic content of any given chromosome(32). In addition, the frequency of stable CAs detectable by WCP-FISH in chromosomes 1-6 and 11, 12, 14, & 19 in cord blood was associated positively with higher levels of PAH measured in maternal prenatal air samples(32). The ambient prenatal PAH measured include 8 potentially carcinogenic PAHs(32), but naphthalene could not be measured in the prenatal samples because of its volatility. These present findings suggest that exposure to some PAHs may lead to clastogenesis. In particular, exposure to naphthalene appears associated with clastogenesis, though at a low rate. Metabolites of other measured PAHs, including fluorene, phenanthrene and pyrene, do not appear to have this association. Our findings are consistent with recent findings of elevated CAs documented in airline workers exposed to jet fuels(44, 45), which are also a source of naphthalene exposure.
Naphthalene, a PAH and IARC-classified possible carcinogen, is the primary ingredient in some mothballs(2). It is a byproduct of wood and gasoline combustion and is contained in gasoline exhaust, jet fuel, and cigarette smoke and is ubiquitous in ambient air with high volumes of vehicular traffic(1). US indoor levels of naphthalene can exceed outdoor ambient levels by 10-fold(6), particularly when naphthalene-containing household products are used(2, 5). Naphthalene like other small PAHs, is found entirely in gas phase rather than as a particulate. One study in US preschoolers found that indoor air levels of naphthalene in daycare and home settings were 5 to 10-fold higher than outdoor air levels (6). Naphthalene levels vary depending on the source of exposure: mothball exposure is equivalent to low level occupational exposure and is likely an important exposure source for children(2, 46). A box of “old fashioned” mothballs contains 396 grams of naphthalene, which is sufficient to raise the average residential indoor air concentration to approximately 200 micrograms per cubic meter over a period of 1 year, though in small homes or apartments this would be expected to be much higher(2, 46). Exposures of this magnitude are commensurate with industrial exposures to coal tar, coke or jet fuels(2). Families in the CCCEH may be culturally predisposed to use naphthalene in their homes(47). Mothball use as air-fresheners has been reported by 27% of NYC families using one inner city emergency room NYC(8). Some Latino households also use mothballs as air-fresheners, pesticides and in traditional remedies(47). Household exposures may present greater risk for inner city school-aged children because they spend larger proportions of their day indoors, largely due to the relative insecurity of their neighborhoods(48).
Despite the widespread exposure to naphthalene, human effects resulting from naphthalene exposure are poorly understood(49). These results are the first to correlate a clastogenic and precarcinogenic effectwith a specific PAH in human populations. By using a marker of excretion, we are able to correlate our results with individual levels of exposure and metabolism(49). Naphthalene undergoes metabolism by the cytochrome P450 monooxygenases to reactive metabolites which may be critical to its toxicity. Naphthalene metabolites could contribute to development of CAs through adduct formation. The (1, 2-naphthoquinonemetabolite of naphthalene has been associated with depurinating adduct formation in rodent models(26). Other metabolites (naphthalene-1, 2-epoxide, 1, 2-dihydrodiol-3,4–epoxide, and 1,4-napthoquinone) may be potential sources of oxidative damage as exposure to these metabolites may result in DNA strand breakage and/or DNA base damage through epoxide formation. DNA damage can also result from bulk DNA-adduct formation. Although in a recent small occupational cohort 2-naphthol levels did not correlate with DNA adducts in peripheral blood mononuclear cells or in urothelial cells, the adducts measured were not naphthalene-metabolite specific(50). Mammalian models have documented naphthalene-metabolite specific adducts in skin cells(21, 26) as well as cytotoxicity and tumor development in cells lining nasal passages and bronchial epithelial cells(23, 51, 52). Our preliminary data suggest that translocations are associated with naphthalene exposure. Together with in vitro data showing toxicity in myeloid precursors after exposure to naphthalene metabolites(22), our results in lymphocytes suggest that naphthalene might also contribute to damage in hematogenous cells.
Our data demonstrate associations between two urinary metabolites of naphthalene and both CAs and translocations. Although 1-naphthol can be derived from both naphthalene and carbaryl, 2-naphthol is derived only from naphthalene. The dose response association seen with translocations in our data is specifically with 2-naphthol. Although the correlation between CA frequency and 2-naphthol is not significant (Table 4), the associations between increasing levels of 2-naphthol and presence of CAs and translocations are stronger than those seen with 1-naphthol (Table 5). Our data suggests that the clastogenicity we document may result from exposure to naphthalene itself. For overall CAs, we do see a significant association between both 1- and 2- naphthol, however as noted above, translocations are considered more predictive of carcinogenic potential. Given the extremely low prevalence of carbaryl in the prenatal air samples in our cohort it is unlikely that children in our cohort are exposed to airborne carbaryl, though they may have some exposure through ingestion of contaminated produce.
The ethnic differences in the levels 1- and 2-naphthol, as well as the differences in associations between naphthol levels and incidence of CAs and especially translocations suggest differences in both exposures to sources of naphthalene, as well as in response to this exposure. However the relatively small number of participants in the two ethnic groups limits our ability to examine this futher. Our results are similar to those noted in the much larger NHANES cohort in which levels of urinary naphthalene metabolites are highest among Mexican Americans(11) suggesting possible cultural variations in patterns of exposure. Differences in response to exposure to naphthalene might reflect differences in incidence of functional polymorphisms of PAH metabolizing enzymes. Polymorphisms in CYP2E1 and GSTM1 have been associated with elevated 2-naphthol levels in coke oven workers(53). Similarly, polymorphisms in CYP1A1, GSTP1, EPHX1, p53 MspI and MTHFR have been associated with translocations in urban smokers occupationally exposed to ambient PAH(54).
Although our study was limited by a relatively small sample size, our findings are consistent with other those of other studies examining adult populations(15,20). The urine samples which we analyzed were collected as single spot measurements; hence they may not be representative. However, because they were collected during home visits,they may reflect exposures present chronically in the homes. Future efforts to build on our initial findings will need to examine larger numbers of children with urinary samples reflecting longer periods of exposure.
In summary, our data suggest that children in the CCCEH cohort have higher levels of urinary naphthalene metabolites and that these are associated with CAs (including translocations), which are precancerous changes in adults. The widespread exposure to naphthalene in the US and worldwide supports the need for further study. Levels of non-occupational exposure are high in the US, particularly in indoor air(7). DNA strand breakage has been associated with occupational exposure to naphthalene(20). We have found chromosomal breaks measured in peripheral blood of school age children associated with increased levels of naphthalene metabolites. Occupational cohort studies have demonstrated that such breaks are predictive of a more than 2-fold increased risk of later cancer(27). While the age difference between the NHANES population and the children in our cohort did not allow for a direct comparison, our data and that of NHANES, nevertheless, document that exposure to naphthalene is widespread in the US(11). Exposure to this potential carcinogen appears particularly elevated in poor US households(7).
In less industrialized societies, cooking with biomass fuel stoves is recognized as a source of indoor air PAH exposure, including naphthalene(3, 4). Recent measurements of Peruvian women using biomass fuels for indoor cooking showed median levels of 1-naphthol and 2-naphthol exceeding the 75th percentile of NHANES. The frequent use of biomass for cooking and heating in less industrialized communities illustrates the need for future studies to confirm the findings presented here and to better assess the risk of occupational and residential exposure to naphthalene worldwide.
Financial Support: NIH grants R01ES12732, U01CA159157, 5P01ES09600, R01 ES013163, P50 ES015905, 5RO1ES08977, RO1ES111158, RO1ES012468, and P30 ES09089 US Environmental Protection Agency [(STAR) Grant RD832096, R827027, 8260901, and RR00645], and the New York Community Trust
Conflicts of Interest: none