Prenatal Exposure to Phthalates and Neurodevelopment in the CHAMACOS Cohort.

BACKGROUND: Previous studies suggest that prenatal exposure to phthalates, ubiquitous synthetic chemicals, may adversely affect neurodevelopment. However, data are limited on how phthalates affect cognition, executive function, and behavioral function into adolescence.
OBJECTIVE: We aimed to investigate associations of prenatal phthalate exposure with neurodevelopment in childhood and adolescence in the Center for the Health Assessment of Mothers and Children of Salinas (CHAMACOS) study.
METHODS: We examined associations between maternal urinary phthalate metabolite concentrations measured twice during pregnancy and a range of neurodevelopmental outcomes from ages 7 through 16 y in the CHAMACOS birth cohort (n=334). We used age-specific linear regression models and generalized estimating equation models to assess longitudinal effects and examined differences by sex.
RESULTS: Phthalate metabolites were detected in 88%-100% of samples, depending on the metabolite. Associations of phthalates with neurodevelopmental outcomes were largely null with some noteworthy patterns. Higher prenatal concentrations of metabolites of low-molecular weight phthalates (ΣLMW) were associated with more self-reported hyperactivity [β=0.8, 95% confidence interval (CI): 0.1, 1.4 per 2-fold increase in ΣLMW phthalates], attention problems (β=1.5, 95% CI: 0.7, 2.2), and anxiety (β=0.9, 95% CI: 0.0, 1.8) at age 16. We observed sex-specific differences for the sums of high-molecular-weight and di(2-ethylhexyl) metabolites and cognitive outcomes (e.g., β for Full-Scale IQ for boys=-1.9, 95% CI: -4.1, 0.3 and -1.7, 95% CI: -3.8, 0.3, respectively; β for girls=1.8, 95% CI: 0.1, 3.4 and 1.6, 95% CI: 0.0, 3.2, respectively; p-int=0.01 for both).
CONCLUSION: We found predominantly null associations of prenatal phthalates with neurodevelopment in CHAMACOS, and weak associations of ΣLMW phthalates with internalizing and externalizing behaviors in adolescence. No previous studies have examined associations of prenatal phthalate exposure with neurodevelopment into adolescence, an important time for manifestations of effects. https://doi.org/10.1289/EHP5165.

Introduction

Phthalates are a group of chemicals used in multiple consumer products (Hauser and Calafat 2005). Low-molecular-weight (LMW) phthalates are used in fragrances, cosmetics, and shampoos (ATSDR 1995, 2001; Harley et al. 2017), and personal care products appear to be a primary source of exposure (Duty et al. 2005; Ejaredar et al. 2015). High-molecular-weight (HMW) phthalates are common plasticizers in products such as food packaging, building materials, medical devices, and toys (Ejaredar et al. 2015; Harley et al. 2017). Phthalates are not covalently bound to the plastics that they soften and can easily leach into the environment (Braun et al. 2013; Meeker et al. 2009). Exposure to phthalates is ubiquitous in the U.S. population (Chopra et al. 2014) and occurs via ingestion, inhalation, and dermal absorption (Adibi et al. 2003; Rudel et al. 2003). A recent examination of five cycles of the National Health and Nutrition Examination Survey (NHANES) found that 10 different phthalate metabolites were detected in of participants between 2001 and 2010 (Zota et al. 2014).

Although phthalates have short half-lives in the body and are rapidly excreted (ATSDR 1995, 2001, 2002; Meeker et al. 2009), humans are chronically exposed from common consumer goods, including plastics, personal care products, and food packaging. Phthalates are endocrine disrupting chemicals (EDCs) that cross the placenta, exposing the developing fetus (Silva et al. 2004; Wittassek et al. 2009). The Chronic Hazard Advisory Panel of the U.S. Consumer Product Safety Commission identified fetal development as the most vulnerable target of toxicity for phthalates (Lioy et al. 2015), and the nervous system may be particularly susceptible due to rapid brain development during the prenatal period. Animal and epidemiologic studies have shown that neurotoxic effects of phthalates may be mediated by antiandrogenic activity (Borch et al. 2006; Weiss 2012), alterations in thyroid function (Boas et al. 2010; Gao et al. 2017), and disruption of brain dopaminergic activity (Bellinger 2013; Tanida et al. 2009).

Several epidemiological studies have evaluated associations between prenatal phthalate exposure and neurodevelopmental outcomes among children followed up to age 10 (Braun et al. 2014, 2017; Engel et al. 2010; Factor-Litvak et al. 2014; Gascon et al. 2015; Kobrosly et al. 2014; Lien et al. 2015; Miodovnik et al. 2011; Shin et al. 2018; Whyatt et al. 2012), with inconsistent findings that vary by phthalate metabolite and child sex (Braun et al. 2013). Although previous studies have reported associations of prenatal urinary phthalate concentrations with poorer cognition (Factor-Litvak et al. 2014), social cognition (Miodovnik et al. 2011), and executive function (Engel et al. 2010) and more internalizing and externalizing behaviors (Engel et al. 2010; Kobrosly et al. 2014; Lien et al. 2015; Whyatt et al. 2012), others have found associations with improved cognitive performance (Braun et al. 2017) or null associations with social cognition outcomes (Braun et al. 2014; Shin et al. 2018).

To our knowledge, no studies have examined the associations of prenatal phthalate exposure with neurodevelopment measured longitudinally during childhood and into adolescence—information that is important for evaluating the potential long-term impact of these chemicals. We examined associations of prenatal phthalate exposure with cognition, executive function, and behavior outcomes assessed from ages 7 through 16 y in the Center for the Health Assessment of Mother and Children of Salinas (CHAMACOS) birth cohort study. We hypothesized that higher prenatal phthalate concentrations would be associated with adverse neurodevelopment during childhood and adolescence.

Methods

Study Population

CHAMACOS is a longitudinal birth cohort study examining the health effects of prenatal and early life environmental exposures among Mexican-American children in California’s Salinas Valley. Subject recruitment and procedures for CHAMACOS have been described elsewhere (Eskenazi et al. 2004, 2006). Briefly, eligible pregnant women (i.e., , gestation, Spanish- or English-speaking, qualified for low-income health insurance, and planning to deliver at the county hospital) were recruited in community clinics between September 1999 and December 2000. Of the 601 women initially enrolled, 527 (88%) remained in the study and delivered a live-born singleton.

We conducted interviews with mothers at two prenatal study visits ( and 26 wk gestation), shortly after delivery, and when children were age 6 months, and 1, 2, 3.5, 5, 7, 9, 10.5, 12, 14, and 16 y. We also assessed CHAMACOS children’s growth and development from ages 6 months to 16 y. We restricted current analyses to children born to mothers with measures of prenatal urinary phthalate metabolites who completed at least one neurodevelopmental assessment at age 7 (), 9 (), 10.5 (), 12 (), 14 (), or 16 y (). In total, 334 children (56% of the initial cohort) had prenatal phthalate data and completed at least one assessment included in these analyses (total sample size exceeds sample size at any individual time point because some participants only completed tests at one time point; 334 unique participants provided usable data from at least one visit).

The University of California Berkeley Committee for the Protection of Human Subjects approved all study activities, and we obtained written informed consent from all mothers. We also obtained child verbal assent at age 7, 9, and 10.5 y, and child written assent at age 12, 14, and 16 y. The Centers for Disease Control and Prevention (CDC) deferred to the University of California Berkeley IRB as the IRB of record.

Neurodevelopmental Outcomes

Bilingual, bicultural psychometricians, trained and supervised by a clinical neuropsychologist, administered neuropsychological tests and computer-based tasks in the child’s dominant language in a quiet room free from distraction. We obtained additional information on children’s behavior across multiple settings with rating scales administered to the parent at all study visits (7, 9, 10.5, 12, 14 and 16 y), the teacher at the 7-y visit, and the child (self-report) at the 10.5-, 14-, and 16-y visits. Outlined below are the instruments we used to assess cognition, executive function, social cognition, and behavior in CHAMACOS children.

Executive Function

Behavior Rating Inventory of Executive Function (BRIEF) (Gioia et al. 2000).

Parents of CHAMACOS children completed the BRIEF when their children were age 7, 9, and 12 y. Teachers completed the BRIEF when children were 7 y old. We examined age- and sex-standardized scores (T-scores; , ) across two indices (the Behavioral Regulation Index and the Metacognition Index) and one summary score (Global Executive Composite).

NEPSY tower (Korkman et al. 1998).

At age 9, children completed the NEPSY tower, which assesses planning, monitoring, self-regulation, and problem solving and yields a single scaled score (, ).

Wisconsin Card Sort Task-64: Computer version 2 – research edition (WCST) (Heaton 2000).

At ages 9 and 12 y, children completed the WCST, a computerized test that measures skills around strategic planning, ability to shift cognitive strategies, and impulse control. We examined T-scores for errors and perseverative errors (, ).

Cognition

Weschler Intelligence Scale for Children, fourth edition (WISC-IV) (Weschler 2003).

Study staff administered the WISC-IV at the 7- and 10.5-y study visits. Children were administered the WISC-IV in English (33.3% of participants) or Spanish (66.7% of participants) at age 7 y. All children were tested in English at age 10.5 y. We calculated scores for Full-Scale IQ (FSIQ) and four subscales: Verbal Comprehension (VCIQ), Perceptual Reasoning (PRIQ), Working Memory (WMIQ), and Processing Speed (PSIQ). We standardized scores against U.S. population-based norms for English- and Spanish-speaking children (, ).

Social Cognition

Evaluación neuropsicológica del niño (ENI) (Matute et al. 2007).

Children completed the ENI at age 9 y. In this test, children were shown eight different photographs and scored on how well they identified the mental state of others (e.g., happy, sad, angry, scared). Participants received a score of 1 for correctly identifying the expression and a score of 0 for incorrectly identifying the expression ().

NEPSY-II Affect Recognition subtest (Korkman et al. 2007).

Children completed the NEPSY-II Affect Recognition at age 12 y. In this test, children had to: a) identify whether two photographs depicted faces with the same affect; b) select two faces with the same affect from three to four photographs; c) select one of four faces that depicted the same affect as the face at the top of the page; and d) view a photograph of a face briefly and select two faces that depicted the same affect as the face previously viewed. Participants received a score of 1 for correctly identifying the expression and a score of 0 for incorrectly identifying the expression ().

Social Responsiveness Scale, version 2 (SRS-2) (Constantino and Gruber 2012).

At the 14-y visit, parents completed the SRS-2, a 65-item rating scale developed to assess quantitative traits related to Autism Spectrum Disorder (ASD) in population-based samples (Constantino and Gruber 2012). Parents were asked the frequency that their child exhibited specific behaviors, such as avoiding social behavior with peers or adults, over the previous 6 months (, , , and ), and we computed sex-standardized SRS total T-scores (, ).

Attention and Behavior

Behavior Assessment System for Children, second edition (BASC-2) and Self-Report of Personality (SRP) (Reynolds and Kamphaus 2004).

Parents completed the BASC-2 when children were age 7, 10.5, 14, and 16 y. Teachers completed the BASC-2 when children were 7 y old. Children completed specific scales of the BASC-2 Self-Report of Personality (SRP) at 10.5 and 14 years of age and completed a full SRP at 16 years of age. We examined parent- and teacher-reported scores from four individual scales (hyperactivity, attention problems, depression, and anxiety) and two composite scales (internalizing and externalizing problems). We examined self-reported scores for the internalizing problems composite scale (there was no externalizing composite score for the SRP) and the hyperactivity, attention problems, depression, and anxiety subscales. BASC-2 data were examined as age- and sex-standardized T-scores (, ).

Conners’ Attention Deficit Hyperactivity Disorder (ADHD)/DSM-IV Scales, parent versions (CADS) (Conners 2001).

Parents completed the CADS when children were ages 7, 9, and 12 y old. Teachers completed the CADS at the 7-y study visit. We computed age- and sex-standardized T-scores for the four CADS subscales (Conners’ ADHD index, and DSM-IV-based inattentive, hyperactive/impulsive subscales, and total ADHD) (, ).

Conners’ Continuous Performance Test, version 5 (CPT II) (Conners and MHS Staff 2000).

At 9 and 12 years of age, children completed the CPT-II, a computerized test that assesses hit rate, accuracy, and impulse control. We examined sex- and age-standardized T-scores (, ) for errors of commission (false positives), errors of omission (false negatives), and continuous ADHD Confidence Index score. The ADHD Confidence Index score indicates the probability that children are correctly classified as having clinical ADHD.

Phthalate Exposure Assessment

Mothers provided spot urine samples in polypropylene containers at each of the two prenatal study visits ( and 26 wk gestation) (). After collection, study staff aliquoted urine into glass vials and stored them at until shipment on dry ice to the CDC for analysis. Urine samples were analyzed with online solid phase extraction–isotope-dilution high-performance liquid chromatography–electrospray ionization-tandem mass spectrometry (Silva et al. 2007) to quantify concentrations of 11 phthalate metabolites from eight parent compounds: monoethyl phthalate [MEP, metabolite of diethyl phthalate (DEP)]; mono-n-butyl phthalate [MBP, metabolite of di-n-butyl phthalate (DnBP)]; monoisobutyl phthalate [MiBP, metabolite of diisobutyl phthalate (DiBP)]; monobenzyl phthalate [MBzP, metabolite of butylbenzyl phthalate (BBzP)]; four metabolites of di(2-ethylhexyl) phthalate (DEHP): [mono(2-ethylhexyl) phthalate (MEHP), mono (2-ethyl-5-hydroxyhexyl) phthalate (MEHHP), mono(2-ethyl-5-oxohexyl) phthalate (MEOHP), and mono(2-ethyl-5-carboxypentyl) phthalate (MECCP)]; mono(carboxyoctyl) phthalate [MCOP, metabolite of diisononyl phthalate (DiNP)]; mono(carboxynonyl) phthalate [MCNP, metabolite of diisodecyl phthalate (DiDP)]; and mono-3-carboxypropyl phthalate (MCPP, metabolite of several HMW phthalates and a minor metabolite of DBP). Quality control procedures included the use of laboratory, calibration standards, and quality controls of high and low concentrations. Limits of detection (LODs) ranged from 0.2 to for individual metabolites.

Covariate Data Collection

Study staff administered structured questionnaires to mothers at each study visit to collect information on a variety of factors, including maternal and child demographics; maternal parity; prenatal diet and smoking, alcohol and illicit drug use; mode of delivery; duration of breastfeeding; parental marital status, maternal education, and employment; and household income. We administered the Peabody Picture Vocabulary Test (PPVT)-Revised (Dunn and Dunn 1981) to estimate maternal receptive vocabulary (6-month and 9-y study visits), the Center for Epidemiologic Studies Depression Scale (CES-D) (Radloff 1977) to assess maternal depression (1-, 3-, 7-, and 9-y visits), and the Home Observation for the Measurement of the Environment-Short Form (HOME-SF) (Caldwell and Bradley 1984) to assess enrichment in the home (6-month, 1-, 2-, 3.5-, 7-, 9-, and 10.5-y visits). We abstracted medical information, such as birth weight and gestational duration, from prenatal and delivery medical records.

We examined potential confounding by other prenatal exposures for which we have reported associations with adverse neurodevelopment in CHAMACOS, including organophosphate pesticides (OPs) (Bouchard et al. 2011; Eskenazi et al. 2007; Marks et al. 2010), organochlorines (OCs) (Eskenazi et al. 2006; Gaspar et al. 2015), polybrominated diphenyl ether flame retardants (PBDEs) (Eskenazi et al. 2013; Sagiv et al. 2015), and manganese (Mn) (Mora et al. 2015). Detailed methods for prenatal biospecimen collection and quantification of these chemicals have been described previously (Bradman et al. 2005; Eskenazi et al. 2006; Eskenazi et al. 2013; Mora et al. 2015). Briefly, we quantified prenatal urinary dialkyl phosphate (DAP) metabolite concentrations as a measure of OP exposure in the same two maternal pregnancy urine samples we used to measure phthalate metabolites (collected at 13 and 26 wk gestation) (Bradman et al. 2005). We also measured OCs (Eskenazi et al. 2006) and PBDEs (Eskenazi et al. 2013) in pregnancy [] serum samples, or in maternal delivery samples for a subset of women () without pregnancy samples. We assessed prenatal exposure to Mn in children’s deciduous teeth (Mora et al. 2015).

Statistical Analysis

We averaged phthalate biomarker concentrations across the two urine samples to better estimate exposure throughout pregnancy (Hoppin et al. 2002) and to normalize the residuals and reduce the influence of the outliers. For concentrations below the LOD, we used the instrumental reading value, when available, and imputed nondetectable concentrations (without an instrumental reading) using maximum likelihood estimation following the log-normal distribution (Lubin et al. 2004).

We categorized phthalate metabolites based on their similarity in chemical structure and biological activity (Teitelbaum et al. 2008) as: a) molar sums of metabolites of LMW () phthalates (i.e., MEP, MBP, and MiBP) or of metabolites of HMW phthalates () (i.e., MBzP, MCPP, MCOP, and MCNP); and b) the molar sum of DEHP metabolites (; i.e., MEHP, MEHHP, MEOHP, and MECPP). We also looked at individual phthalate metabolites ().

We examined associations of average prenatal urinary phthalate biomarker concentrations (individual metabolites and summed concentrations) with neurodevelopmental outcomes assessed at a single time point (i.e., SRS, ENI, NEPSY-II, BASC-2 teacher-report, CADS teacher-report, and SRP internalizing scale) using multivariable linear regression and at multiple time points (i.e., WCST, BRIEF, WISC-IV, CADS, CPT-II, and other BASC-2 scales) using generalized estimating equations (GEE). If associations of phthalates with repeated measures of an outcome changed appreciably over time, we presented estimates from the linear regression analyses for each time point separately. To evaluate the presence of nonlinearity in exposure–outcome associations, we modeled phthalate concentrations categorized into tertiles.

We selected the following covariates a priori using a directed acyclic graph (See Figure S1): maternal age at enrollment (continuous), education (categorical: grade, 7th–12th grade, completed high school), country of birth (categorical: Mexico vs. other), years in the United States (continuous), and depression status at the time of assessment (dichotomous: vs. points in CES-D); child sex (dichotomous) and exact age at assessment (continuous); language of assessment or language of interview for parent-reported outcomes (dichotomous); HOME z-score at time of assessment (continuous); household income at the time of assessment (categorical: at or below poverty line vs. above poverty line); and psychometrician. Because the CPT-II and WCST were computerized tasks, we additionally adjusted these outcomes for children’s video game usage (average hours per week) at age 9 as reported by mothers. We imputed missing values for covariates (all missing) using data from the nearest available visit. If values for a missing covariate were not available from an earlier or later study visit, we randomly selected a value from the dataset ( participant missing HOME score and maternal depression values at the 14- and 16-y visits; participants missing maternal PPVT for sensitivity analyses).

We evaluated effect modification of the exposure–outcome associations by child sex using an augmented product term approach (Buckley et al. 2017) in which we specified a model including product terms between sex and each of the covariates, including sex. Interactions were assessed using sex-metabolite product terms from the same model and were considered statistically significant if .

We conducted sensitivity analyses to assess the robustness of our results. First, we fitted our regression models excluding preterm births (; defined as delivery ) and low birth weight (LBW) children (; defined as birthweight ) ( LBW and preterm). The number of children excluded varied by neurodevelopmental test because not all study participants completed each test. Second, we adjusted our regression models for additional potential confounders [i.e., breastfeeding duration ( vs. ) and maternal receptive vocabulary at the 9-y visit (PPVT score: , 75–99, ) by adding them individually to models. Last, we examined the confounding effects of prenatal exposure to other known neurotoxicants by adding prenatal PBDEs, DAPs, OCs, and Mn concentrations individually to our adjusted models. These additional neurotoxicants were modeled continuously and log-transformed (PBDEs, DAPs, and OCs transformed to the scale and Mn transformed to the scale). PBDEs were modeled as the lipid-adjusted sum of four congeners (, , , ), and OCs were modeled as the lipid-adjusted sum of dichlorodiphenyltrichloroethane (p,p′-DDT, o,p′-DDT), and dichlorodiphenyldichloroethylene (p,p′-DDE) from maternal serum collected at 26 wk gestation. Total DAP metabolite levels were calculated as the sum of six nonspecific urinary OP metabolites, averaged across two prenatal urine samples. All levels below the LOD were set at .

Results

Table 1 shows the sociodemographic characteristics of mother–child pairs from the initial cohort who delivered a live-born singleton () and participants with prenatal phthalate data who completed at least one neurodevelopmental test at age 7 y (). Table S1 shows the sociodemographic characteristics of participants with prenatal phthalate data who completed at least one neurodevelopmental test at age 9, 10.5, 12, 14, or 16 y. Among those with at least one neurodevelopmental assessment at age 7 y, most mothers were born in Mexico (86%), had not completed high school (78%), and had a family income below the U.S. poverty threshold (70%) (Table 1). Nearly 53% of CHAMACOS children were female, and 49% were breastfed for (Table 1). The standardized scores for each neurodevelopmental test are shown in Table S2.

Table 1

Sociodemographic characteristics [n (%) or median (P25–P75)] of live-born singletons from the initial CHAMACOS mother–child cohort () and study participants with prenatal urinary phthalate metabolites who completed at least one of the neurobehavioral assessments at ages 7 ().

Characteristic	Live-born singletons n (%) or Median (P25–P75)	Children with prenatal phthalates and at least one assessment at 7-y visit N (%) or Median (P25–P75)
Maternal/household characteristics
Age at enrollment (y)	25 (22–29)	25.5 (22–29)
Education
≤6th grade	228 (43.3)	142 (44.1)
7th–12th grade	192 (36.4)	110 (34.2)
Completed high school	107 (20.3)	70 (21.7)
Receptive vocabulary (PPVT score) at 9-y visit		98 (80–108)
Missing (n)b	—	23
Country of birth
Mexico	444 (84.3)	277 (86.0)
Other	83 (15.8)	45 (14.0)
Years in U.S.
≤5	270 (51.2)	151 (46.9)
6–10	115 (21.8)	84 (26.1)
≥11	142 (27.0)	88 (27.0)
Parity
0	180 (34.2)	102 (31.7)
≥1	347 (65.8)	220 (68.3)
Smoking during pregnancy
No	496 (94.1)	309 (96.0)
Yes	31 (5.9)	13 (4.0)
Maternal depression at 9-year visit (≥16 CES-D score)
No	225 (42.7)	233 (72.4)
Yes	78 (14.8)	81 (25.1)
Missing (n)b	224 (42.5)	8 (2.5)
Household income at 10.5-year visit
At or below poverty level	242 (45.9)	225 (69.9)
Above poverty level	95 (18.0)	97 (30.1)
Missing (n)b	190 (36.1)	0 (0.0)
Child characteristics
Child’s sex
Boy	263 (49.9)	153 (47.5)
Girl	264 (50.1)	169 (52.5)
Birth weight (grams)	3,440 (3,155–3,780)	3,437.5 (3,170–3,785)
Gestational age at delivery (wk)	39 (38–40)	39 (38–40)
Breastfeeding duration (months)
≤6	311 (59.0)	163 (50.6)
>6	205 (38.9)	159 (49.4)
Missing	11 (2.1)	0 (0.0)
Age at assessment (y)
7-y assessment	—	7.0 (7.0, 7.1)
Language of assessment		—
English	—	106 (33.8)
Spanish	—	208 (66.2)
HOME Score Assessment		0.1 (−0.6–0.8)
Missing (n)b	—	—

Note: —, no data; CES-D, Center for Epidemiologic Studies Depression Scale; , number of study participants; PPVT, Peabody Picture Vocabulary Test.

At age 7, a total of 322 mothers and 314 youth completed at least one neurodevelopmental assessment.

Missing data for children followed-up were imputed with values collected on these variables at earlier or later time points for all analyses.

Phthalate metabolites were detected in 88%–100% of samples, depending on the metabolite (Table 2). Phthalate metabolite concentrations were generally similar to those measured in NHANES participants around the same time period (CDC 2018) (see Table S3 for uncorrected phthalate metabolite concentrations). Between-person variance exceeded within-person variance by a factor of two to eight (Table 2). Intraclass correlation coefficients (ICC) varied from 0.11 to 0.33 (Table 2). Spearman’s correlation coefficients among different phthalate metabolites ranged from 0.11 to 0.98 (see Table S4).

Table 2

Distribution of phthalate biomarker concentrations (specific-gravity-corrected) measured in maternal urine samples collected at two time points during pregnancy, CHAMACOS ().

Phthalate biomarkera	% >LOD		σbtw2d	σwithin2d	ICCd	Average of two measurements
	1st measurementb	2nd measurementc				GM (GSD)	Min	P25	P50	P75	Max
ΣLMW	N/A	N/A	0.94	2.14	0.31	1.5 (32.9)	0.1	0.7	1.4	2.9	105.7
MEP	100.0	99.7	1.26	2.59	0.33	241.7 (3.3)	14.3	108.5	223.1	501.9	20,462.0
MBP	98.8	100.0	0.30	2.29	0.11	28.4 (2.4)	1.3	16.2	26.8	47.6	529.8
MiBP	92.9	96.1	0.65	2.79	0.19	3.4 (2.7)	0.1	1.8	3.3	6.7	138.0
ΣHMW	N/A	N/A	0.34	1.27	0.21	0.3 (2.1)	0.0	0.2	0.3	0.5	5.1
MBzP	98.5	98.7	0.88	2.01	0.31	8.9 (2.6)	0.5	4.9	9.0	17.7	137.0
MCPP	88.3	93.6	0.62	3.02	0.17	2.2 (2.3)	0.0	1.4	2.4	3.8	28.5
MCOP	96.9	96.5	0.40	1.83	0.18	3.8 (2.1)	0.2	2.4	3.8	5.6	93.2
MCNP	95.7	96.8	0.43	1.46	0.23	2.3 (2.0)	0.2	1.5	2.3	3.4	42.7
ΣDEHP	N/A	N/A	0.38	1.43	0.21	0.2 (2.2)	0.0	0.1	0.2	0.4	5.0
MEHP	88.6	92.0	0.59	2.80	0.17	4.5 (2.6)	0.2	2.6	4.4	7.7	141.3
MEHHP	100.0	99.0	0.49	1.82	0.21	18.9 (2.4)	0.9	11.3	17.9	32.6	458.4
MECPP	100.0	100.0	0.36	1.29	0.22	32.4 (2.2)	4.2	20.9	31.4	49.6	631.8
MEOHP	98.2	98.7	0.52	2.10	0.20	13.8 (2.4)	0.6	8.1	14.0	22.4	335.0

Note: ICC, intraclass correlation coefficient; LOD, limit of detection; MBP, mono-n-butyl phthalate; MBzP, monobenzyl phthalate; MCPP, mono(3-carboxypropyl) phthalate; MCOP, mono(carboxyoctyl) phthalate; MCNP, mono(carboxynonyl) phthalate; MECCP, mono(2-ethyl-5-carboxypentyl) phthalate; MEHP, mono-2-ethylhexyl phthalate; MEHHP, mono(2-ethyl-5-hydroxyhexyl) phthalate; MEOHP, mono(2-ethyl-5-oxohexyl) phthalate; MEP, monoethyl phthalate; MiBP, mono-isobutyl phthalate; , sum of di-2-ethylhexyl phthalate metabolites; , sum of high-molecular-weight phthalate metabolites; , sum of low-molecular-weight phthalate metabolites.

Units are ng/mL for all individual metabolites and nmol/mL for the sums of metabolites (, , ).

Median (range) gestational age at (5.3–28.5) weeks gestation.

Median (range) gestational age at (21.8–39.5) weeks gestation.

Variances between- and within-woman and ICC were calculated and reported for specific-gravity adjusted urinary phthalate concentrations (nonaveraged).

Our analysis of tertiles provided evidence of nonlinearity for some associations, such as for and with WCST executive function outcomes (see Table S5). However, given that most exposure–outcome associations were linear (see Tables S5–S11), we included phthalate biomarker concentrations parameterized as continuous variables in all models, with point estimates representing the change in outcome for each 2-fold increase in biomarker concentrations. In our main analyses, we present results for the phthalate biomarkers , , and . Results for individual phthalate metabolites are included in Supplementary Material.

Most associations between prenatal concentrations of , , and with executive function outcomes were null in both combined (Table 3) and sex-stratified (see Table S12) analyses. When stratified by sex, we found that higher prenatal concentrations were associated with better scores for perseverative errors among boys (, 95% CI: 0.3, 2.5), but not among girls (, 95% CI: , 1.1; ; see Table S12).

Table 3

Adjusted associations [ (95% CI)] of prenatal urinary phthalate biomarker concentrations (nmol/mL; and specific gravity-adjusted) with executive function and cognition outcomes at 7, 9, 10.5, and/or 12 y using GEE models, CHAMACOS.

Outcomes	Orientationb	n	k	ΣLMW	ΣHMW	ΣDEHP
Executive function
WCST (T-score) (9, 12 y)
Errors	(−)	593	318	0.2 (−0.4, 0.8)	0.5 (−0.4, 1.4)	0.5 (−0.3, 1.3)
Perseverative Errors	(−)	593	318	0.7 (−0.1, 1.4)	0.7 (−0.6, 1.9)	0.6 (−0.5, 1.8)
BRIEF—parent report (T-score) (7, 9, 12 y)
Behavioral Regulation Index	(+)	923	331	0.1 (−0.5, 0.6)	0.1 (−0.8, 1.0)	0.0 (−0.9, 0.8)
Metacognition Index	(+)	922	330	−0.4 (−1.0, 0.1)	−0.1 (−1.0, 0.9)	−0.1 (−1.0, 0.7)
Global Executive Composite	(+)	923	331	−0.3 (−0.8, 0.3)	0.0 (−1.0, 1.0)	−0.1 (−1.0, 0.8)
NEPSY Tower (scaled score)c (9 y)	(−)	313	313	0.1 (−0.1, 0.3)	0.1 (−0.2, 0.4)	0.1 (−0.2, 0.4)
Cognitiond
WISC-IV Full-Scale IQ (scaled scores) (7, 10.5 y)	(−)	589	321	−0.2 (−1.0, 0.6)	0.0 (−1.4, 1.4)	0.1 (−1.3, 1.4)
Verbal comprehension IQ	(−)	621	324	−0.4 (−1.1, 0.4)	−0.3 (−1.6, 1.0)	−0.3 (−1.5, 1.0)
Perceptual reasoning IQ	(−)	621	324	0.2 (−0.7, 1.2)	0.4 (−1.1, 1.9)	0.3 (−1.1, 1.7)
Working memory IQ	(−)	593	323	−0.6 (−1.4, 0.1)	−0.1 (−1.5, 1.2)	−0.1 (−1.4, 1.2)
Processing speed IQ	(−)	593	323	0.2 (−0.4, 0.9)	0.5 (−0.7, 1.7)	0.5 (−0.6, 1.7)

Note: Models were adjusted for maternal age at enrollment, education, country of birth, years in the U.S., depression at time of assessment; child sex, child age at time of assessment, language of assessment, HOME score, and household income at time of assessment. WCST models were also adjusted for children’s video game usage. BRIEF, Behavior Rating Inventory Executive Function; k, number of children with data for at least one time point; , number of observations from all time points; NEPSY, A Developmental Neuropsychological Assessment; , sum of metabolites of low-molecular-weight phthalates; , sum of metabolites of high-molecular-weight phthalates; , sum of di(2-ethylhexyl) phthalate metabolites; WCST, Wisconsin Card Sort Task-64: computer version 2—research edition; WISC-IV, Wechsler Intelligence Scale for Children 4th edition.

Separate models created for each sum of metabolites (, , ).

() Higher scores indicate poorer performance/more symptomatic behavior; () lower scores indicate poorer performance/more symptomatic behavior.

NEPSY tower measured at one time point and modeled using linear regression.

Data also presented in Figure 1.

Figure 1.

Adjusted associations [ (95% CI)] for WISC-IV IQ scores per 2-fold increase in prenatal (A) , (B) , and (C) concentrations (nmol/mL; and specific gravity-adjusted) among all children and stratified by sex using GEE models. Models adjusted for maternal age at enrollment, education, country of birth, years in the United States, depression at time of assessment; child sex, child age at time of assessment, language of assessment, HOME score, and household income at time of assessment. Sex-specific effect estimates and p-int values obtained from models including cross-product terms between child sex and the exposure and child sex and each of the covariates. p-int represents interaction of exposure and sex obtained from these models. Data also shown in Tables 3 and S12.

We found mostly null associations of prenatal , , and concentrations with IQ scores in analyses of boys and girls combined (Table 3). However, when we stratified by child’s sex, we observed that higher prenatal concentrations were associated with lower FSIQ (, 95% CI: , 0.3) and WMIQ (, 95% CI: , 0.0) scores among boys but higher FSIQ, WMIQ, and PSIQ scores among girls (, 95% CI: 0.1, 3.3; , 95% CI: 0.1, 3.4; and , 95% CI: 0.2, 2.9; respectively; all ; see Figure 1 and Table S12). Similarly, higher concentrations were associated with decreased WMIQ scores in boys (, 95% CI: , 0.1) and increased FSIQ, WMIQ, and PSIQ scores among girls (, 95% CI: 0.0, 3.2; , 95% CI: 0.1, 3.2; and , 95% CI: 0.1, 2.8; respectively; all ; see Figure 1 and Table S12). Among all children, MEP concentrations were associated with slightly decreased WMIQ scores (, 95% CI: , 0.1) and MiBP concentrations were associated with slightly increased PSIQ scores (, 95% CI: 0.0, 1.8; see Table S13). Effect estimates for VCIQ were null for all metabolites in both stratified and sex-stratified analyses (Table 3, Table S12, Table S13).

Most associations of prenatal phthalate concentrations with social cognition outcomes hovered at the null in both combined and sex-stratified analyses. Higher concentrations were associated with slightly better scores on the ENI assessment at 9 y among all children (, 95% CI: 0.0, 0.2; see Table 4) and among girls (, 95% CI: 0.0, 0.4; see Table S14).

Table 4

Adjusted associations [ (95% CI)] of prenatal urinary phthalate biomarker concentrations (nmol/mL; and specific gravity-adjusted) with behavior and social cognition outcomes at 7, 9, 10.5, 12, 14, and/or 16 y using GEE models, CHAMACOS.

Outcomes	Orientationb	n	k	ΣLMW	ΣHMW	ΣDEHP
Social cognitionc
SRS Total Score (14 y)	(+)	245	245	0.4 (−0.2, 0.9)	−0.3 (−1.1, 0.5)	−0.3 (−1.1, 0.5)
ENI (9 y)	(−)	313	313	0.0 (−0.1, 0.1)	0.1 (−0.1, 0.2)	0.1 (0.0, 0.2)
NEPSY-II (12 y)	(−)	310	310	−0.1 (−0.3, 0.2)	−0.3 (−0.7, 0.1)	−0.2 (−0.5, 0.2)
Behavior
BASC-2—parent-report (T-score)
Internalizing problems (7, 10.5, 14, 16 y)	(+)	1,226	328	0.4 (−0.1, 1.0)	0.5 (−0.4, 1.4)	0.4 (−0.5,1.2)
Depression scalec (7 y)	(+)	322	322	0.4 (−0.1, 1.0)	0.4 (−0.5, 1.3)	0.3 (−0.6, 1.1)
Anxiety scalec (7 y)	(+)	313	313	0.3 (−0.3, 1.0)	0.8 (−0.4, 1.9)	0.6 (−0.5, 1.7)
Externalizing problems (7, 10.5, 14, 16 y)	(+)	1,219	328	0.1 (−0.4, 0.5)	0.2 (−0.6, 0.9)	0.1 (−0.6, 0.7)
Hyperactivity scale (7, 10.5, 14, 16 y)	(+)	1,226	328	0.0 (−0.4, 0.4)	−0.1 (−0.7, 0.6)	−0.1 (−0.8, 0.5)
Attention problems scale (7, 10.5, 14, 16 y)	(+)	1,226	328	0.0 (−0.5, 0.5)	−0.1 (−1.0, 0.7)	−0.1 (−0.9, 0.7)
BASC-2—teacher-report (T-score)c
Internalizing problems (7 y)	(+)	265	265	−0.7 (−1.6, 0.2)	−0.4 (−1.8, 1.0)	−0.3 (−1.6, 1.0)
Depression scale (7 y)	(+)	265	265	−0.6 (−1.4, 0.1)	−0.2 (−1.4, 0.9)	−0.2 (−1.4, 0.9)
Anxiety scale (7 y)	(+)	265	265	−0.9 (−1.8, 0.1)	−0.8 (−2.1, 0.5)	−0.7 (−2.0, 0.6)
Externalizing problems (7 y)	(+)	265	265	−0.1 (−0.8, 0.6)	0.0 (−1.0, 1.0)	0.2 (−0.7, 1.1)
Hyperactivity scale (7 y)	(+)	265	265	0.0 (−0.7, 0.7)	−0.2 (−1.4, 0.9)	−0.1 (−1.1, 0.9)
Attention problems scale (7 y)	(+)	265	265	0.2 (−0.8, 0.4)	−0.5 (−1.4, 0.4)	−0.3 (−1.2, 0.5)
CADS—parent-report (T-score)
ADHD Index (7, 9, 12 y)	(+)	920	332	−0.3 (−0.7, 0.1)	−0.2 (−1.0, 0.5)	−0.2 (−1.0, 0.5)
DSM-IV Total Scale (7, 9, 12 y)	(+)	921	332	−0.3 (−0.7, 0.1)	−0.1 (−1.0, 0.7)	−0.2 (−1.0, 0.5)
Inattentive scale (7, 9, 12 y)	(+)	920	332	−0.3 (−0.7, 0.1)	−0.3 (−1.0, 0.5)	−0.3 (−0.9, 0.4)
Hyperactive/impulsive scale (7, 9, 12 y)	(+)	920	332	−0.2 (−0.7, 0.2)	0.0 (−0.9, 0.9)	−0.1 (−1.0, 0.7)
CADS—teacher-report (T-score)c
ADHD Index (7 y)	(+)	261	261	−0.4 (−1.2, 0.5)	−0.5 (−1.9, 0.9)	−0.4 (−1.6, 0.9)
DSM-IV Total Scale (7 y)	(+)	260	260	−0.2 (−0.9, 0.5)	−0.2 (−1.4, 1.0)	−0.1 (−1.2, 1.0)
Inattentive scale (7 y)	(+)	264	264	−0.1 (−0.8, 0.5)	−0.1 (−1.2, 0.9)	−0.1 (−1.0, 0.9)
Hyperactive/impulsive scale (7 y)	(+)	264	264	−0.1 (−0.8, 0.6)	0.1 (−1.1, 1.3)	0.2 (−0.9, 1.3)
CPT-II (T-score)
Errors of omission (9, 12 y)	(+)	595	317	0.9 (0.0, 1.8)	−0.1 (−1.2, 1.1)	−0.2 (−1.2, 0.9)
Errors of commission (9, 12 y)	(+)	595	317	0.3 (−0.2, 0.8)	−0.1 (−1.0, 0.8)	−0.3 (−1.1, 0.6)
ADHD confidence index (9, 12 y)	(+)	596	317	0.7 (−0.5, 1.9)	−1.0 (−2.7, 0.8)	−1.0 (−2.6, 0.6)

Note: Models were adjusted for maternal age at enrollment, education, country of birth, years in the U.S., depression at time of assessment; child sex, child age at time of assessment, language of assessment, HOME score, and household income at time of assessment. CPT-II models were also adjusted for children’s video game usage at time of assessment. ADHD, Attention Deficit Hyperactivity Disorder; BASC-2, Behavior Assessment System for Children, 2nd edition; CADS, Conners' ADHD/DSM-IV Scales; CPT-II, Continuous Performance Test, 2nd edition; DSM-IV, Diagnostic and Statistical Manual of Mental Disorders, 4th edition; ENI, Evaluación Neuropsicológica del Niño; k, number of children with data for at least one time point; , number of observations from all time points; NEPSY-II, A Developmental Neuropsychological Assessment, 2nd Edition; , sum of metabolites of low-molecular-weight phthalates; , sum of metabolites of high-molecular-weight phthalates; , sum of di(2-ethylhexyl) phthalate metabolites. SRS, Social Responsiveness Scale, version 2.

Separate models created for each sum of metabolites (, , ).

() Higher scores indicate poorer performance/more symptomatic behavior; () lower scores indicate poorer performance/more symptomatic behavior.

Measured at one time point and modeled using linear regression.

Behavior

Among all children, higher prenatal phthalate concentrations were associated with more errors of omission (higher T-scores) on the performance-based CPT-II (; 95% CI: 0.0, 1.8) measured at 9 and 12 y (Table 4) and poorer self-reported behaviors measured using the BASC-2 SRP scale, including more hyperactivity (; 95% CI: 0.1, 1.4), attention problems (; 95% CI: 0.7, 2.2), anxiety (; 95% CI: 0.0, 1.8), and overall internalizing problems on the composite scale (; 95% CI: 0.4, 1.9) measured at 16 y (Table 5). Similar, albeit weaker, trends were observed for parent-reported BASC-2 results modeled using GE; however, associations of phthalates with most teacher-reported behaviors were null or in the opposite direction of parent- and self-reported results (Table 4). We did not observe consistent sex-specific associations for behavior outcomes in GEE (Table S14) or linear regression models (Table S15). Prenatal MEP, MBzP, MCPP, and MCOP concentrations were associated with increased scores for parent-reported internalizing problems and/or errors of commission (Table S16). Similarly, prenatal concentrations of MEP and MCPP were associated with increased self-reported internalizing problems at age 16 (Table S17).

Table 5

Adjusted associations [ (95% CI)] of prenatal urinary phthalate biomarker concentrations (nmol/mL; and specific gravity-adjusted) with self-reported BASC-2 behavioral outcomes at 10.5, 14, and 16 y using linear regression models, CHAMACOS.

Outcome	Orientationb	n	ΣLMW	ΣHMW	ΣDEHP
10.5-y assessment
Internalizing problems	(+)	—	—	—	—
Depression scale	(+)	289	0.5 (−0.1, 1.1)	0.7 (−0.5, 1.9)	0.6 (−0.5, 1.8)
Anxiety scale	(+)	289	0.3 (−0.3, 1.0)	0.5 (−0.6, 1.5)	0.4 (−0.6, 1.4)
Externalizing problems
Hyperactivity scale	(+)	299	0.2 (−0.5, 0.8)	0.5 (−0.6, 1.5)	0.3 (−0.7, 1.3)
Attention problems scale	(+)	290	−0.1 (−0.8, 0.7)	−0.4 (−1.5, 0.8)	−0.4 (−1.4, 0.7)
14-y assessment
Internalizing problems	(+)	—	—	—	—
Depression scale	(+)	301	0.5 (−0.1, 1.2)	0.6 (−0.6, 1.8)	0.5 (−0.6, 1.6)
Anxiety scale	(+)	300	0.4 (−0.2, 1.1)	−0.3 (−1.3, 0.7)	−0.4 (−1.3, 0.6)
Externalizing problems
Hyperactivity scale	(+)	—	—	—	—
Attention problems scale	(+)	—	—	—	—
16-y assessment
Internalizing problems	(+)	283	1.2 (0.4, 1.9)	0.4 (−0.7, 1.4)	0.4 (−0.6, 1.3)
Depression scale	(+)	286	0.7 (−0.1, 1.5)	0.2 (−0.8, 1.2)	0.3 (−0.7, 1.2)
Anxiety scale	(+)	286	0.9 (0.0, 1.8)	0.7 (−0.4, 1.8)	0.6 (−0.5, 1.7)
Externalizing problems
Hyperactivity scale	(+)	285	0.8 (0.1, 1.4)	0.0 (−1.0, 1.0)	−0.2 (−1.2, 0.8)
Attention problems scale	(+)	286	1.5 (0.7, 2.2)	−0.2 (−1.2, 0.8)	−0.3 (−1.2, 0.6)

Note: Models were adjusted for maternal age at enrollment, education, country of birth, years in the U.S., depression at time of assessment; —, no data; child sex, child age at time of assessment, language of assessment, HOME score, and household income at time of assessment. BASC-2, Behavior Assessment System for Children, 2nd edition; , number of children; , sum of metabolites of low-molecular-weight phthalates; , sum of metabolites of high-molecular-weight phthalates; , sum of di(2-ethylhexyl) phthalate metabolites.

Separate models created for each sum of metabolites (, , ).

() Higher scores indicate poorer performance/more symptomatic behavior; () lower scores indicate poorer performance/more symptomatic behavior.

Sensitivity Analyses

In general, the point estimates did not change appreciably in sensitivity analyses after a) excluding preterm births and LBW children (see Tables S18–S20), and b) adjusting for additional potential confounders, including maternal receptive vocabulary (see Tables S21–S23) and breastfeeding duration (see Tables S24–S26). Associations of prenatal phthalate concentrations with self-reported hyperactivity, depression, and anxiety were attenuated in models adjusted for coexposure to PBDEs (Tables S27–S29), OP and OC pesticides (Tables S30–S35), and Mn (Tables S36-38), with all CI including the null.

Discussion

In this prospective cohort of low-income Mexican-American children, we observed primarily null associations of prenatal urinary phthalate biomarker concentrations with a wide range of measures of childhood and adolescent cognition and behavior. We did find suggestive associations of prenatal phthalates with more parent- and self-reported internalizing problems and poorer scores on performance-based behavioral assessments (i.e., CPT-II errors of omission). We also observed that prenatal and concentrations were associated with slightly higher IQ scores among girls and lower IQ scores among boys.

The previous literature from longitudinal birth cohort studies evaluating prenatal phthalate exposure and childhood neurodevelopment has produced mixed results. With respect to cognitive function, the Columbia Center for Children’s Environmental Health (CCCEH) study reported that prenatal concentrations of the LMW phthalate metabolites MBzP and MiBP were inversely associated with IQ scores among 328 children age 7 y (Factor-Litvak et al. 2014). Conversely, the Health Outcomes and Measures of the Environment (HOME) study found that higher prenatal concentrations of LMW phthalate metabolites, including MBzP and MBP, were associated with improved performance on the Virtual Morris Water Maze among 198 8-y-old children, particularly among boys (Braun et al. 2017). We also found evidence of better cognition in association with higher prenatal phthalate exposure in sex-stratified analyses in CHAMACOS; however, we observed that prenatal and concentrations were associated with slightly higher IQ scores among girls and lower IQ scores among boys.

Only one previous study, the Mount Sinai Children’s Environmental Healthy study, examined associations of prenatal phthalate exposure with executive function and found that higher metabolite concentrations from third-trimester maternal urine were associated with poorer BRIEF global executive composite index scores in 188 children ages 4–9 y (Engel et al. 2010). In contrast, we found null associations for phthalates and BRIEF behavioral regulation and global executive composite scores, and slightly better scores on the parent-reported BRIEF metacognition index.

Three previous studies have reported associations of prenatal phthalates with more externalizing behaviors, including aggression, hyperactivity, and conduct problems (Engel et al. 2010; Kobrosly et al. 2014; Lien et al. 2015). The Mount Sinai study reported associations of prenatal LMW phthalate concentrations with parent report of increased aggression, attention, and conduct problems on the BASC among children ages 4–9 y (Engel et al. 2010). A study of 122 mother–child pairs in Taiwan found that prenatal concentrations of LMW phthalate metabolites, as well as DEHP metabolites, were associated with parent report of more aggressive and delinquent behaviors on the Child Behavior Checklist (CBCL) at 8 y (Lien et al. 2015). In the multicenter Study for Future Families of 153 children ages 6 to 10 y in 4 U.S. states, prenatal MBP, a LMW phthalate, was associated with more parent-reported inattention, rule-breaking behavior, aggression, and conduct problems on the CBCL (Kobrosly et al. 2014). In addition, prenatal MBzP, a HMW phthalate, was associated with more parent-reported oppositional and conduct problems, but only among boys (Kobrosly et al. 2014). Only the Spanish INfancia y Medio Ambiente (INMA)-Sabadell birth cohort study () found essentially null associations for prenatal phthalate biomarkers and all behavioral outcomes, including ADHD-related behaviors, measured at 4 and 7 y (Gascon et al. 2015). In the CHAMACOS study, we observed modest associations of phthalates with attention problems, including poorer performance on the CPT-II at ages 9 and 12 and more symptomatic self-reported BASC-2 hyperactivity and attention problems scores at age 16. Associations with all other externalizing behaviors, including those from teacher-, parent-, and self-report, were essentially null.

Results from previous studies are less consistent with respect to internalizing behaviors. Although the Mount Sinai study reported associations of prenatal phthalate concentrations with more anxiety and depression among all children (Engel et al. 2010), the Study for Future Families found associations with less anxiety among girls (Kobrosly et al. 2014), and the Taiwanese study reported null associations for prenatal phthalates with all internalizing behaviors (Lien et al. 2015). Furthermore, the CCCEH study reported associations of prenatal MBP and MBzP concentrations (metabolites of LMW phthalates) with more internalizing behaviors among all children, with stronger associations observed for MBzP among girls (Whyatt et al. 2012). Associations of prenatal phthalates and BASC self-report of internalizing behaviors at age 16 were among the strongest in the CHAMACOS study, though associations with BASC parent report were considerably weaker, and BASC teacher-report associations were in the opposite direction. Although these results may seem paradoxical, they are largely in line with previous studies that have reported poor multiple informant agreement for parent-, teacher-, and child-reported behaviors, with worse concordance among participants with internalizing disorders (Miller et al. 2014; Verhulst and Akkerhuis 1989). Although externalizing problems may be more easily observed by others, a child can choose not to disclose feelings of anxiety or depression to teachers or caregivers (Salbach-Andrae et al. 2009). Previous studies indicate that teacher–youth agreement may be less than parent–youth agreement (Youngstrom et al. 2000), particularly for internalizing disorders (Salbach-Andrae et al. 2009), which is largely consistent with findings from our study. We observed the strongest findings for self-reported behavior at age 16, and evidence suggests that discrepancies in parent- and self-report and the reliability of self-reported behaviors increase with age (Edelbrock et al. 1985; Verhulst and Akkerhuis 1989). Although reports from multiple informants provide a more comprehensive picture of behaviors of children and adolescents throughout time, adolescents may be a more reliable source about their own internalizing behavior.

Consistent with the results from a study of 201 children age 3 y from the Markers of Autism Risk in Babies—Learning Early Signs (MARBLES) cohort (Shin et al. 2018), a study of 175 children ages 4–5 y from the HOME cohort (Braun et al. 2014), and the Spanish INMA-Sabadell birth cohort (Gascon et al. 2015), we found null associations of prenatal phthalate exposure with social cognition outcomes. In contrast, a study of 137 children ages 7–9 y from the Mount Sinai cohort found that higher prenatal phthalate concentrations were associated with poorer SRS scores (Miodovnik et al. 2011). To our knowledge, ours is the first study to investigate phthalate-related associations with tests of affect recognition (i.e., ENI and NEPSY-II), which may provide more comprehensive and objective data than parent-report alone.

Potential reasons for the heterogeneity in our findings and those from previous studies include differences in a) sample size, b) timing and number of prenatal exposure measurements, c) specific phthalate metabolites measured, d) neurodevelopmental tests administered, e) age of child at neurodevelopmental assessments, and f) sociodemographic characteristics that may influence phthalate exposure. For example, we assessed a larger diversity of neurodevelopmental outcomes than many previous studies assessed, and ours is the only study to examine associations of prenatal phthalates exposure with behavior and executive function using computer-based assessments. Additionally, we had a larger sample size than those in some previous investigations and assessed phthalate exposure from two prenatal urine samples, whereas many previous studies relied on one measurement. Notably, some of our strongest findings were for self-reported behavioral outcomes at age 16, and to our knowledge, ours is the first study to examine associations of prenatal phthalate exposure and neurodevelopment past age 10 y.

Our study has several strengths and limitations. The longitudinal design of CHAMACOS and collection of rich data, including biological specimens, a wide array of neurodevelopmental measures, behavioral measures from multiple reporters (e.g., parents, teachers, and participants), and covariates, allowed for a very thorough and nuanced examination of the potential impacts of in utero phthalate exposure throughout childhood and adolescence. Ours is the first study to our knowledge to investigate the impacts of prenatal phthalate exposure and neurocognitive outcomes during adolescence, allowing us to examine the persistence of effects identified in cohorts of younger children. In addition, although previous studies have relied solely on parent-report of executive function, behavior, and social cognition, we directly assessed participants with respect to executive function (WCST and NEPSY Tower), attention and impulse control (CPT-II), and social cognition (ENI and NEPSY Affect Recognition). These arguably more objective, performance-based tests contribute to the richness of our neurodevelopmental assessments. Furthermore, to our knowledge, we are the first longitudinal study to examine the effects of prenatal phthalate exposure on adolescent self-reported behavior, which may provide more nuanced information on internalizing behaviors such as anxiety and depression.

Although the collection of rich neurodevelopmental data across various domains is a primary strength of our study, it also makes interpretation of our results more difficult, as demonstrated by inconsistency in our findings across these multiple outcomes. More important, we conducted a large number of analyses with multiple comparisons, which could produce spurious associations by chance alone. Therefore, we were careful to report patterns in our results rather than highlighting isolated findings. Overall, the richness and diversity of our outcomes allow us to conclude with some confidence that prenatal exposure to select phthalates is not strongly associated with neurodevelopment in our cohort.

The prenatal period has been identified as the most vulnerable window of neurotoxicity (Lioy et al. 2015); however, emerging evidence indicates that childhood phthalate exposure may be associated with adverse cognitive outcomes among children ages 2 to 12 y (Cho et al. 2010; Factor-Litvak et al. 2014; Huang et al. 2015; Kim et al. 2017; Li et al. 2019). We did not measure childhood phthalate concentrations in our cohort, and it is possible that postnatal exposures could affect neurodevelopment in this population, particularly during puberty, a period during which the brain is developing rapidly and may be particularly susceptible to EDCs (Wang et al. 2016). Previous research has shown sex-specific changes in internalizing and externalizing behaviors, executive function, and social cognition during puberty (Blakemore et al. 2010; Gur and Gur 2016; Spear 2013), and a toxicology study found that DEHP exposure during puberty was associated with increased anxiety among female mice (Wang et al. 2016). In addition to prenatal exposures, future studies should consider also assessing phthalate concentrations during childhood and adolescence to identify critical periods of susceptibility.

Our study and others have shown relatively low correlation between phthalate measurements collected at multiple times during pregnancy (Gascon et al. 2015) and poor reproducibility between measurements (Johns et al. 2015). Other studies have also suggested that phthalate metabolite concentrations can vary depending on the time of day at which the urine sample was collected (Silva et al. 2004) and that exposure biomarker patterns may vary, depending on the primary source of phthalate exposure (Johns et al. 2015; Preau et al. 2010). In addition to introducing nondifferential exposure misclassification that may have biased our results toward the null, the nonpersistent nature of phthalates makes it difficult to identify windows of susceptibility based on the timing of prenatal exposure (Braun et al. 2014). Future research investigating these exposure–outcome relationships should include a more critical evaluation of the most robust sampling strategy (Shin et al. 2019) (i.e., spot, first morning void, 24-h collection) to reduce exposure measurement error for the phthalate metabolite of interest.

Overall, we found mostly null associations of prenatal phthalate exposure with child and adolescent neurodevelopmental outcomes in the CHAMACOS cohort, though we observed some suggestive associations of prenatal LMW phthalate biomarker concentrations with more internalizing and externalizing behaviors, particularly from self-reported and performance-based assessments. These findings add to a growing literature addressing the potential developmental neurotoxicity of phthalate exposure.

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Click here for additional data file.