Predictors of urinary phthalate biomarker concentrations in postmenopausal women.

Table 1 describes the personal, behavioral, and reproductive characteristics of the study group included in these analyses at WHI enrollment. Participants were, on average, 62.5 years old (SD 6.9), and the majority was of white race (83.2%). Participants were nearly evenly distributed between enrollment in the Clinical Trial (47.3%) and Observational Study (52.7%) and across BMI categories. Participants had a low level of current alcohol use (32.8% current non-drinkers) and smoking (6.2% current smokers), a high level of current HT use (38.6%), and a high neighborhood SES score (73.1, SD 8.7). Descriptive statistics of phthalate biomarkers concentrations are presented in Table 2 , calculated from all measurements of phthalate biomarker concentrations in samples from baseline, year 1, and year 3 using GEE models to account for repeated measurements within a participant. Exposure to phthalates was common but highly variable. For example, MEP was detected in 100% of samples with a broad range of concentrations (12.7 ng/mL, 5 th percentile – 773.0 ng/mL, 95 th percentile). Concentrations of phthalate metabolites from the same parent compound (e.g. DiBP) were highly correlated with one another (e.g. MHiBP and MiBP, r=0.95). MBzP was highly correlated with MHBP concentrations (r=0.74). MCNP was significantly correlated with MCOP (r=0.40) and MCPP (r=0.36), and MCOP and MCPP also were highly correlated (r=0.60). Concentrations of other phthalate biomarkers were not strongly correlated with one another. Table 3 presents the results of our parsimonious, multivariable regression modeling of MEP, MBzP, MCOP, MCNP, and MCPP concentrations. Predictors of MEP concentrations were race/region (higher among non-whites), education level (lower among college educated women), BMI (lower among obese women), and current alcohol intake (higher with increased intake). MBzP concentrations were inversely related to age. Non-white/Northeast and non-white/South participants had lower MBzP compared to white/Northeast, while MBzP was highest among white/West. Increased BMI was positively associated with MBzP, while higher neighborhood SES and higher quality diet were associated with lower MBzP. Increased parity and history of hysterectomy were both associated with higher MBzP concentrations. MCOP concentrations were negatively associated with age and were highest among white/Northeast women and lowest among non-white/South women. Overweight and obese women also had higher MCOP concentrations compared to underweight/normal weight women. MCNP concentrations were lowest in non-white/South and white/South women compared to other race/region groups and were positively associated with BMI category. Physical activity was positively associated with MCNP concentrations, while history of hysterectomy was associated with lower MCNP concentrations. MCPP was inversely associated with age, higher among Whites compared to non-whites, positively associated with BMI category, and positively associated with physical activity. Predictors of the summary measures of exposure to DBP, DiBP, and DEHP in multivariable regression models are shown in Table 4 . ΣDBP concentrations were inversely associated with age. Participants from the West region had higher ΣDBP concentrations, with non-white/West women having the highest concentrations. Women reporting current alcohol intake of 1–6 drinks per week had higher estimated ΣDBP concentration than non-drinkers. Likewise, current smokers had higher ΣDBP concentrations as compared to never smokers. ΣDBP concentration was higher among women with a hysterectomy and lower among those self-reporting diabetes. ΣDiBP concentration was lowest among white/South women and positively associated with education level. Overweight women had significantly higher ΣDiBP concentration as compared to the underweight/normal and obese women. Better diet quality was predictive of lower ΣDiBP concentrations. Women who used unopposed estrogen either in the past or currently had higher ΣDiBP concentration than never users. ΣDEHP concentrations were lower among women from the South region. BMI category was positively associated with ΣDEHP concentration, while better diet quality was negatively associated with ΣDEHP. ΣDEHP concentrations also were lower among women with a history of diverticulitis compared to those without this condition. Although all data and urine samples from breast cancer cases were collected prior to their diagnosis (average 6.2 years prior), we repeated our analysis in the subset of women selected as controls. When fitting the same statistical models developed among the full cohort, the magnitude and direction of associations were nearly identical among the subset of controls as in the full sample. We also repeated our model building process restricting to the subset of controls. In general, we found very similar results to those obtained with the full sample ( Supplementary Tables 1 & 2 ). Some differences were noted, however. MEP concentrations were also predicted by smoking (positive) and higher diet quality score (negative), while BMI was not predictive of MEP concentration among controls. Hysterectomy was not predictive of MBzP concentrations among controls. MCOP was predicted by smoking status (positive). MCNP was not predicted by hysterectomy status, though a positive association with estrogen + progestin use and a negative association with stomach ulcer were observed among controls. MCPP concentrations in controls were not predicted by BMI category, though a negative association with SES was observed. The model for ΣDBP among controls did not include smoking status or diabetes. Finally, the model for ΣDEHP did not include diverticulitis, but a positive association with thyroid disease was observed. The models for ΣDiBP among controls and the full sample were identical.

Participants in the WHI were recruited from 40 clinical centers nationwide in the United States between October 1, 1993 and December 21, 1998, and details relevant to participant recruitment have been reported previously (Women’s Health Initiative 1998). Briefly, the WHI consisted of three clinical trials (CT): postmenopausal hormone therapy (HT; N=27,347), dietary modification (DM; N=48,835), and calcium/vitamin D supplementation (CaD; N=36,282); participants were able to take part in more than one trial. Women who were either not interested or not eligible for the CT were enrolled in an observational study (OS; N=93,676). A total of 161,808 women participated in the WHI. All participants were between the ages of 50 and 79 at the time of enrollment. Women at three WHI clinical sites (N=11,020) also participated in a bone mineral density substudy, and these were the only sites at which urine samples were collected. Participants in this analysis were those selected as either cases (N=419) or controls (N=838) for a nested case-control study of phthalate exposure and breast cancer risk within the WHI ( Figure 1 ). Eligible women for the parent study were those without a self-reported history of cancer, except for non-melanoma skin cancer, and who had sufficient urine available from baseline and the year 3 clinic visit. Cases were all adjudicated cases of invasive breast cancer occurring among women at the three bone density substudy sites after AV3 and during their WHI follow-up through 2013. Cases diagnosed prior to AV3 were excluded. The final (AV3) urine sample was provided an average of 6.2 years (SD 4.3) prior to breast cancer diagnosis among cases. Controls were selected using incidence density matching from among eligible participants who were not diagnosed with breast cancer or any other cancer, except for nonmelanoma skin cancer, during WHI follow-up and had urine sample available. Those eligible were individually matched on enrollment date, length of follow-up, age at enrollment, and WHI study arm in a 2:1 ratio to cases. When more than two eligible controls existed as a potential match for a case, two controls were randomly selected from the pool of eligible controls. First morning void urine samples were collected at home and processed within 30 minutes after participants arrived at each clinic visit. The samples were frozen and stored until they were thawed and processed for this analysis. WHI recommended, but did not require, the use of polypropylene urine collection containers, which are phthalate-free. Two clinical centers did not use the specific containers recommended, and the composition of the containers that were used is unknown. However, all sites used polypropylene centrifuge tubes and cryovials. Concerns over contamination are minimal, however, because we measured metabolites (which reflect endogenous exposure and are unlikely to originate from external contamination) rather than the parent phthalate (which would be the contaminant from the collection vial). The present analysis included urine samples collected at baseline (N=1,257) and at the year 3 (AV3) clinic visit (N=1,191); additionally, we included urine samples collected from the year 1 (AV1) clinic visit for women enrolled in the WHI CT (N=570). All participants provided written informed consent upon enrollment into the WHI. The WHI was approved by institutional review boards (IRB) at each clinical center. Additionally IRB approval for the present study was obtained from the University of Massachusetts Amherst. The involvement of the Centers for Disease Control and Prevention (CDC) laboratory in the analysis of samples did not constitute engagement in human subjects research. Participants provided data at an initial enrollment clinic visit and at the year 3 clinic visit; additionally, WHI CT participants provided data at the year 1 clinic visit. Pertinent to this analysis, data were collected via self-reported questionnaire on age, race, educational attainment, marital status, occupation, alcohol use, smoking duration and amount, total physical activity, hormone therapy (HT) use, pregnancy history, breastfeeding history, infertility history, hysterectomy, and other medical history. Because race/ethnicity was strongly related to U.S. census region due to the nature of the WHI study design for the bone density centers, we created a joint race/region variable for use in this analysis. We included conditions that have been related to phthalate exposure in prior studies (thyroid disease, based on reported associations between phthalate exposure and thyroid hormone levels ( Boas et al. 2012 ; Meeker and Ferguson 2011 ), and diabetes ( Sun et al. 2014 )) or that are treated with medications known to contain high concentrations of phthalates ( Hauser et al. 2004 ; Hernandez-Diaz et al. 2009 ) (stomach ulcer, diverticulitis, and ulcerative colitis). Height and weight were measured by trained study personnel and used to calculate BMI. Medication use and dietary intake are complex exposures that have been previously associated with phthalate exposure and will be addressed in separate analyses; however, we did explore menopausal hormone therapy use and a measure of diet quality as predictors of phthalate metabolites in the current analysis. The Healthy Eating Index 2005 (HEI-2005) score was calculated as a measure of diet quality based on the U.S. Department of Agriculture 2005 Dietary Guidelines for Americans from self-reported food frequency questionnaire data ( George et al. 2014 ; Guenther et al. 2008 ); higher scores on the HEI-2005 reflect a better quality diet as defined by the USDA 2005 Dietary Guidelines (e.g. consuming the recommended amounts of fruits versus not consuming any fruit). We utilized a previously calculated assessment of neighborhood socioeconomic status ( Griffin et al. 2013 ). Updated data on BMI, alcohol use, smoking status, physical activity, hysterectomy, and hormone therapy use were available at years 1 and 3 and were incorporated in the analysis. WHI followed a standard urine collection, processing, and storage protocol at the three clinical centers that collected urine samples. Urine samples were collected at home and processed within 30 minutes after participants arrived at their clinic visit. Urine samples were centrifuged for 5 minutes at 1330 x g and 1.8mL aliquots were frozen and then shipped to McKesson Bioservices packed in dry ice via overnight FedEx where they were stored at −70 °C. A panel of thirteen phthalate metabolites was measured in baseline, year 1, and year 3 urine samples at the CDC: mono-ethyl phthalate (MEP), mono-n-butyl phthalate (MBP), monohydroxybutyl phthalate (MHBP), mono-isobutyl phthalate (MiBP), mono-hydroxyisobutyl phthalate (MHiBP), monobenzyl phthalate (MBzP), mono(3-carboxypropyl) phthalate (MCPP), four DEHP metabolites (mono(2-ethylhexyl) phthalate [MEHP], mono(2-ethyl-5-hydroxyhexyl) phthalate [MEHHP], mono(2-ethyl-5-oxohexyl) phthalate [MEOHP], mono(2-ethyl-5-carboxypentyl) phthalate [MECPP]), mono-carboxyoctyl phthalate (MCOP), and monocarboxynonyl phthalate (MCNP). Phthalate biomarkers were measured after enzymatic hydrolysis of the conjugated metabolites followed by on-line solid phase extraction coupled to high performance liquid chromatography-electrospray ionization-isotope dilution tandem mass spectrometry. Complete details of the assay are published online at https://wwwn.cdc.gov/nchs/data/nhanes/2013-2014/labmethods/PHTHTE_H_MET_Phthalates.pdf . The limits of detection (LODs) were in the low ng/mL range (0.2 ng/mL – 0.6 ng/mL). We imputed phthalate metabolite concentrations below the limit of detection (LOD) to a value equal to the LOD divided by the square root of two, following the protocol used for NHANES (Hornung and Reed 1990): MBP (n=2, 0.07%), MEHP (n=19, 0.63%), MHBP (n=13, 0.43%), MHiBP (n=47, 1.56%), MiBP (n=14, 0.46%); all concentrations of MBzP, MCNP, MCOP, MCPP, MECPP, MEHHP, MEOHP, MEP, and creatinine were >LOD. Study samples were randomly distributed through the analytical batches, with cases and matched controls analyzed together. A blinded 10% quality control sample was included, and estimated CVs were as follows: MBP 5.4%, MBzP 6.1%, MCNP 4.7%, MCOP 6.3%, MCPP 5.8%, MECPP 4.3%, MEHHP 5.4%, MEHP 19.5%, MEOHP 6.0%, MEP 3.1%, MHBP 9.0%, MHiBP 21.9%, MiBP 10.3%. All laboratory staff were masked to the identity, disease status, and demographic and risk factor characteristics of the samples. Creatinine was also measured by using an enzymatic assay at CDC on a Roche Modular P Chemistry Analyzer (Indianapolis, IN). The LOD for creatinine was 1 mg/dL and the CV was 2.5%. Phthalate metabolite concentrations were natural log transformed to improve normality. Phthalate metabolites were analyzed individually and using summary scores. For metabolites of the same parent compound, we created a summary biomarker by dividing each metabolite of a single parent by its molecular weight and then summing across metabolites ( Hauser et al. 2016 ; Watkins et al. 2014 ). Sum of di-n-butyl phthalate (ΣDBP) was calculated as the molar sum of MBP and MHBP, sum of di-isobutyl phthalate (ΣDiBP) was calculated as the molar sum of MiBP and MHiBP, and sum of di(2-ethylhexyl) phthalate (ΣDEHP) was calculated as the molar sum of MEHP, MEHHP, MEOHP, and MECPP. Pearson correlation coefficients were calculated to evaluate correlations among the phthalate biomarker concentrations, using the individual replicate measures. We fit generalized estimating equation (GEE) models, using an identity link and exchangeable correlation, to explore the characteristics that predict phthalate exposures. . This modeling approach allowed for each observation to contribute to the analysis as many replicate measurements as available and included updated covariate information for each timepoint (e.g. age, BMI) as appropriate. We initially fit single predictor models for each phthalate biomarker concentrations including creatinine and a single covariate. We considered the following possible predictors: age (continuous, years), race and clinical site (white/Northeast, non-white/Northeast, white/South, non-white/South, white/West, non-white/West), education (<high school, high school/some college, college degree and higher), marital status (single/divorced/widowed, married/marriage-like relationship), occupation (managerial/professional, technical/sales/administrative, service/labor, homemaker only), BMI (underweight/normal [<25 kg/m 2 ], overweight [25-<30 kg/m 2 ], obese [≥30 kg/m 2 ]), current alcohol intake (non-drinker, <1 drink per week, 1–6 drinks per week, ≥7 drinks per week), smoking status (never smoked, past smoker, current smoker), total physical activity (continuous, MET-h/wk) unopposed estrogen use (never, past, current), estrogen + progestin use (never, past, current), any hormone therapy use (never, past, current), parity (nulliparous, 1–3 children, ≥4 children), breastfeeding duration (never breastfed, 1–6 months, 7–12 months, 13–23 months, ≥24 months), infertility (no, yes), hysterectomy (no, yes), ever had thyroid disease (no, yes), ever had diabetes (no, yes), ever had stomach ulcer (no, yes), ever had diverticulitis (no, yes), ever had ulcerative colitis (no, yes), healthy eating index score (continuous), and neighborhood SES index (continuous). We then fit multivariable regression models considering first all predictors with a p value less than 0.25 from the bivariate GEE models. We used a backward selection approach to select a final, parsimonious model for each phthalate biomarker where all variables significant at the p≤0.05 level were retained; age was included in all models regardless of statistical significance. We calculated predicted means and 95% confidence intervals (CI) for each variable based on the final parsimonious models, with all covariates held at their means. For categorical variables, we calculated the mean for each level of the variable; for continuous variables, we calculated means at the midpoint value of each quartile. As a sensitivity analysis, we repeated our analyses among the subsample of participants selected as controls. All analyses were performed using Stata version 15.0 (Stata Corp, College Station, TX).

In a multi-ethnic population of postmenopausal women, we observed many common exposures that predicted urinary phthalate metabolite concentrations. It is noteworthy that predictors of some phthalate biomarkers (MCOP, MCNP, and MCPP) were generally similar, perhaps reflecting commonalities in sources of exposure to the parent compounds, which are commonly used in soft plastics (e.g. tubing, food packaging) ( Committee on the Health Risks of Phthalates 2008 ). Notably, concentrations of MBzP, MCOP, MCPP, and ΣDBP were all inversely associated with age, though age was not significantly associated with other biomarker concentrations. The lower concentrations of some phthalate biomarkers observed in older age groups may result from differences in exposure patterns and/or slower metabolism of phthalates with older age, though additional work would be useful in confirming and understanding these associations. Race/region was a significant predictor of most phthalate biomarkers. Interestingly, concentrations of many biomarkers were highest among participants from the West, and lowest among women from the South; these findings suggest that patterns of exposure may differ across regions and/or the differing racial/ethnic backgrounds of participants from those regions. Consistent with prior reports (Centers for Disease Control and Prevention 2018), concentrations of MEP were highest among non-white women. Higher neighborhood SES was predictive of lower MBzP, while higher education was predictive of lower MEP and higher ΣDiBP; these demographic factors were not predictive of other phthalate metabolites in multivariable models. Although the exact mechanisms and/or sources responsible are unclear, our results suggest variation in phthalate exposure across many demographic factors. BMI was positively associated with MBzP, MCOP, MCNP, MCPP, and ΣDEHP, though was inversely associated with MEP. These findings are in agreement with prior work ( Buser et al. 2014 ; Hatch et al. 2008 ; Hatch et al. 2010 ; Yaghjyan et al. 2015 ). Phthalates may act as obesogens and contribute to the development of obesity; there is some evidence that some phthalates can trigger adipogenesis through activation of peroxisome proliferator-activated receptors ( Feige et al. 2007 ; Hurst and Waxman 2003 ). However, phthalate biomarker concentrations in the obese may instead be elevated because of their obesity, either due to differences in metabolism of these compounds or from differential exposure patterns among the obese. Future prospective studies would be useful to establish whether elevated phthalate biomarker concentrations are a cause or an effect of obesity. MEP and ΣDBP were higher among women consuming alcohol versus non-drinkers. Current smoking predicted higher ΣDBP concentrations. A higher quality diet was predictive of lower MBzP, ΣDiBP, and ΣDEHP concentrations. Recent studies have reported presence of phthalates in food ( Schecter et al. 2013 ; Serrano et al. 2014 ). Concentrations of phthalates in food groups vary across studies, but meats and dairy appear to be common sources of phthalates, including DEHP, DBP, butylbenzyl phthalate, and DiBP ( Schecter et al. 2013 ; Serrano et al. 2014 ). Physical activity was positively associated with concentrations of MCNP and MCPP. A prior study in a sample of Australian men reported slightly higher total phthalate metabolite concentration associated with insufficient physical activity, although this association did not attain statistical significance ( Bai et al. 2015 ). The mechanisms linking physical activity and phthalate exposure and/or metabolism are unclear and merit further study. Unopposed estrogen use was positively associated with ΣDiBP concentrations. This finding was surprising given that HT formulations have not been reported to contain phthalates ( Hauser et al. 2004 ; Hernandez-Diaz et al. 2009 ). Interestingly, women reporting a hysterectomy had higher concentrations of MBzP, MCNP, and ΣDBP. Few medical conditions were predictive of urinary phthalate biomarker concentrations; diabetes was inversely associated with ΣDBP and diverticulitis was inversely associated with ΣDEHP. Based on previous reports of phthalate exposure via medications and medical equipment ( Gimeno et al. 2014 ; Green et al. 2005 ; Hauser et al. 2004 ; Hernandez-Diaz et al. 2009 ), we had anticipated that these chronic conditions would be associated with higher phthalate biomarker concentrations, contrary to what we observed; the observed associations may result from misclassification due to our self-reported data or from our definition of exposed as “ever” having these conditions as opposed to currently having them. Interestingly, reproductive characteristics (age at menarche, parity, breastfeeding duration, and infertility) were generally not predictive of phthalate biomarker concentrations, except for a positive association observed between parity and MBzP concentrations. The link between parity and MBzP is not clear, and will require confirmation in future studies. The overall lack of predictive value of the reproductive characteristics, which are factors determined many years prior to sample collection, supports the conclusion that measured phthalate metabolite concentrations are determined by very recent exposures (i.e. within the past day). It is important to consider these results in the context of relevant limitations. First, our study group was comprised of postmenopausal women selected for a nested case-control study of breast cancer within a large, prospective cohort study. Thus, the population is highly selected and may not reflect the general population of U.S. women, although we did observe similar phthalate metabolite concentrations and patterns of association with age and race as reported by contemporary NHANES measurements. Additionally, we observed similar patterns of association when we restricted our analyses to women selected as controls, suggesting that undiagnosed disease and/or risk factor patterns associated with future disease did not appreciably influence our results. Third, phthalate metabolites exhibit considerable within-person variability ( Townsend et al. 2013 ), which may result in exposure misclassification and bias our results towards the null. Thus, we may have failed to identify some weaker predictors of the urinary phthalate biomarkers examined, and the associations we observed may actually be stronger than we report. This may especially be true for lifetime exposures, given that measured phthalate metabolite concentrations reflect only very recent exposure which may not represent typical values in an individual. Additionally, some observed differences between groups were very small (e.g. ΣDiBP: 0.012 ng/mL underweight/normal, 0.013 ng/mL overweight, and 0.014 ng/mL obese) and may be statistically significant, yet not clinically or analytically meaningful. Also, we did not adjust for multiple comparisons; thus, some observed associations may reflect type I error. However, the general consistency of associations across phthalate biomarkers provides reassurance that the associations we observed were not due to chance alone. Finally, given the complexity of assessing medications and diet as exposures, we evaluated only postmenopausal HT use and a summary measure of diet quality in the present study. It is likely that additional features of diet and/or medication use are related to phthalate exposure, and these will be comprehensively evaluated in future work. Our work is strengthened by the large sample size and repeated measurements (1,257 women and 2,991 observations in total) of a broad panel of phthalate biomarkers using first morning void urine samples, which are not often available within large epidemiologic cohorts. The laboratory that quantified the phthalate metabolites is highly experienced with such measurements in biological specimens, and the overall reliability of the assays was excellent. Our work was also enhanced by the wide range of data collected in the WHI, which allowed us to evaluate a broad panel of personal, behavioral, and reproductive characteristics for their association with urinary phthalate metabolite concentrations. Although use of some phthalates has declined in recent years ( Zota et al. 2014 ), phthalate exposure remains ubiquitous in the United States and globally. Understanding the factors that are predictive of phthalate exposure, as well as the consequences of such exposures, is critical for identifying potential high-risk groups with elevated exposure and for protecting public health. Our findings identified a number of factors associated with lower phthalate biomarker concentrations, including older age and engaging in “healthy behaviors” including lower alcohol intake, lower BMI, not smoking, and higher quality diet. We also observed substantial differences in phthalate biomarker concentrations across racial groups and geographic regions. Importantly, while such factors were predictive of urinary phthalate metabolite concentrations, the differences in predicted mean concentrations were often very small across groups defined by these variables. Thus, biological measurements of urinary phthalate metabolites would strengthen future epidemiologic studies.

Increasing scientific evidence supports the endocrine-disrupting and potentially carcinogenic effects of some phthalates, chemicals used in plastics and in a wide variety of consumer products either to increase the flexibility of the plastic or as solvents (e.g. vinyl flooring, cosmetics, medical supplies, medications) ( Koch and Calafat 2009 ). Although nearly all U.S. residents have detectable concentrations of phthalate metabolites in their urine, the concentrations vary widely ( Silva et al. 2004 ). Phthalate exposure can occur through inhalation, ingestion, or transdermal absorption because phthalates are not chemically bound to plastics and thus can be easily released into the environment ( Centers for Disease Control and Prevention 2014 ). Phthalates are rapidly metabolized in the body into their monoesters, a step that can increase their bioactivity ( Frederiksen et al. 2007 ). High molecular weight phthalates undergo further oxidation; phthalate metabolites may also be glucuronidated ( Frederiksen et al. 2007 ; Koch and Calafat 2009 ; Silva et al. 2004 ). Because metabolites are eliminated nearly completely in urine within 24–28 hours after exposure ( Frederiksen et al. 2007 ), measurement of urinary phthalate metabolites gives an accurate assessment of recent exposure to phthalates; such measurements would reflect both ongoing, and potentially low-level exposures, as well as changing exposures over time. Indeed, prior work has established the moderate within-person variability of urinary phthalate biomarker concentrations (Adibi et al. 2008; Braun et al. 2012; Cantonwine et al. 2014 ; Peck et al. 2010; Townsend et al. 2013 ; Watkins et al. 2014 ). Extensive research has documented the endocrine-disrupting effects of phthalates. Phthalates may have important, adverse effects on female reproductive function, although data are not entirely consistent ( Kay et al. 2013 ). Previous studies have related urinary concentrations of various phthalate biomarkers to adverse human health effects in women including endometriosis ( Buck Louis et al. 2013 ; Upson et al. 2013 ; Weuve et al. 2010 ), elevated body mass index (BMI) ( Hatch et al. 2008 ; Trasande et al. 2012 ) and weight gain ( Song et al. 2014 ), diabetes ( James-Todd et al. 2012 ) and insulin resistance ( Trasande et al. 2013 ), and breast cancer (Holmes et al. 2014;) Lopez-Carrillo et al. 2010 ), although a recent study reported no association between urinary phthalate biomarkers and breast cancer risk (Parada et al. 2018). Exposure to phthalates may be related to increased risk of a wide range of chronic health outcomes. Predictors of phthalate exposure are not well understood, though phthalate metabolite concentrations have been associated with diet ( Cantonwine et al. 2014 ; Colacino et al. 2010 ), personal care product use ( Cantonwine et al. 2014 ; Duty et al. 2005 ; Parlett et al. 2013 ), medications ( Hauser et al. 2004 ; Hernandez-Diaz et al. 2009 ), and elevated BMI and body fat ( Hatch et al. 2008 ; Lind et al. 2012 ). We sought to describe personal, behavioral, and reproductive characteristics associated with phthalate metabolite concentrations in an ongoing study nested within the Women’s Health Initiative (WHI).