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  • Open Access
  • Open Peer Review

Concentrations of persistent organic pollutants in maternal and cord blood from the maternal-infant research on environmental chemicals (MIREC) cohort study

  • 1, 5Email author,
  • 1,
  • 1,
  • 2,
  • 2,
  • 3,
  • 1,
  • 1 and
  • 4
Environmental Health201615:59

https://doi.org/10.1186/s12940-016-0143-y

  • Received: 17 July 2015
  • Accepted: 25 April 2016
  • Published:
Open Peer Review reports

Abstract

Background

Pregnant women are an especially important population to monitor for environmental exposures given the vulnerability of the developing fetus. During pregnancy and lactation chemical body burdens may change due to the significant physiological changes that occur. Developmental exposures to some persistent organic pollutants (POPs) have been linked with adverse health outcomes.

Methods

First trimester maternal and cord blood plasma concentrations of several POPs including polychlorinated biphenyls (PCBs), organochlorine pesticides (OCs), polybrominated diphenyl ethers (PBDE)s and perfluoroalkyl substances (PFASs) were measured in samples from 1983 pregnant women enrolled in the Maternal-Infant Research on Environmental Chemicals (MIREC) cohort. Predictors of exposure were also identified.

Results

In maternal plasma, there was >90 % detection for the perfluoroalkyl substances (PFASs) perfluorooctanoic acid (PFOA), perfluoroctane sulfonate (PFOS), perfluorohexane sulfonate (PFHxS), and dichlorodiphenyldichloroethylene (DDE), oxychlordane and PCB 138 and 153. Cord blood plasma had much lower detection rates with low or very limited detection for most PCBs and PBDEs. The PFASs were the most frequently detected (23–64 %) chemical class in cord plasma. In a subset of 1st and 3rd trimester paired samples, PFAS concentrations were found to be strongly correlated and had ICCs ranging from 0.64 (PFOA) to 0.83 (PFHxS). The cord:maternal plasma concentration ratios ranged from 0.14 (PFOS) to 0.87 (oxychlordane, lipid adjusted). Similar to other studies, we found parity, maternal age, income, education, smoking status, pre-pregnancy BMI and fish consumption to be significant predictors for most chemicals. Those participants who were foreign-born had significantly higher concentrations of organochlorinated pesticides and PCBs.

Conclusions

In the MIREC study, multiple chemical contaminants were quantified in the plasma of pregnant women. In cord plasma PFOA had the highest detection rate. However, compared to other Canadian and international population studies, the MIREC participants had lower contaminant concentrations of these substances.

Keywords

  • POPs
  • DDT
  • PCBs
  • PBDEs
  • PFASs
  • Cord plasma
  • Maternal plasma
  • Pregnant

Background

Persistent organic pollutants (POPs), including organochlorine pesticides (OCs), industrial chemicals and their by-products are chemicals that persist in the environment and tend to bioaccumulate, possess toxic properties, and resist degradation [1]. Several biomonitoring studies have measured POPs in human plasma [24], milk [5, 6], and cord blood [79].

Perfluoroalkyl substances (PFASs) are heat stable, non-flammable and able to repel water and oils. They are used in a wide variety of products including non-stick cookware, breathable all weather clothing, wiper blades, wire and cable insulation, fire retardant foams, lubricants, paper coatings, pharmaceuticals, and nail polish [2]. They are very stable compounds and therefore highly persistent in the environment [10]. In 2002, 3M, the main manufacturer of PFOS ceased production in the U.S. and the EPA finalized new rules to help limit the future manufacturing and importation of these substances [11]. Efforts were implemented in 2006 to drastically reduce emissions of PFOA and its precursors by 95 % by 2010 and to work towards eliminating emissions and product content by 2015 [12]. Exposures to humans mainly occur through diet [13, 14].

PBDEs are a class of brominated flame retardants that are environmentally persistent, bioaccumulate and biomagnify in terrestrial food chains [15]. Studies have found PBDEs in fish, dairy products and eggs [16, 17]. House dust [18, 19] has also been suggested as a significant source of exposure, especially for children [20]. The Government of Canada has placed restrictions on some PBDEs under the Canadian Environmental Protection Act, 1999 in order to protect the environment. As of 2008 regulation prohibit the manufacturing of all PBDEs in Canada, and restrict the import and sale of PBDEs in mixtures [21]. Furthermore, as of 2009 there has been a phasing out of penta- and octa-BDEs had occurred in North America, Europe, Australia and Japan [22].

Pregnant women are an especially important population to include in biomonitoring and epidemiological studies given the susceptibility of the developing fetus [10, 23, 24] to the potential adverse health effects arising from exposure to environmental chemicals. During pregnancy and lactation, body burdens of chemicals may change due to the significant physiological changes that occur. The pregnant woman experiences increased blood volume, enhanced metabolism, increased renal perfusion as well as substantial changes to circulating hormones, essential elements and serum lipids [25, 26]. These changes may have an impact on absorption, distribution, metabolism and excretion of environmental contaminants, which has potentially serious implications for developmental exposures of the fetus. Some POP exposures during fetal developmental have been linked with thyroid hormone disruption [23, 2729], adverse birth outcomes [3032], poorer respiratory health [33], obesity [34], and neurotoxicity [35, 36].

This article describes both maternal and cord plasma concentrations of several POPs including polychlorinated biphenyls (PCBs), OC pesticides, polybrominated diphenyl ethers (PBDE)s and perfluoroalkyl substances (PFASs) measured in the Canadian prospective cohort, Maternal-Infant Research on Environmental Chemicals (MIREC). We also explored maternal and infant characteristics to identify elevated exposure groups.

Methods

The MIREC Study is a national-level pregnancy cohort of approximately 2000 women recruited from 10 cities across Canada and has been previously described [37]. The MIREC study is based on a convenience sample and enrolled pregnant women from the general population who were attending prenatal clinics (ultrasound, midwife and/or doctor’s clinics) during the first trimester of pregnancy (6 to <14 weeks) between 2008 and 2011. Research Ethics Board approval was obtained from all participating sites and Health Canada. Women who gave informed consented scheduled visits in each trimester, at delivery and in the postpartum period (up to 8-10 weeks). At each pregnancy visit women completed questionnaires and provided both blood and urine samples. The questionnaires collected information such as sociodemographics, current and previous pregnancies, diet, smoking and lifestyle. Maternal blood was collected in 10 mL K2 EDTA tubes; plasma was transferred into 2.5 mL pre-cleaned glass vials (Supelco®) for the POPs analysis and a 5 mL Sarstedt® tube for the PFASs analysis. Cord blood was collected at delivery using a Baxter bag® and then transferred into tubes as described above for maternal blood. Samples were stored at -20 °C.

In the MIREC study there were close to 300 chemical metabolites measured in maternal urine, blood, cord blood, meconium and breast milk which have been described elsewhere [37]. These chemicals were chosen based on evidence of potential reproductive toxicity, and valid laboratory methods available for biomarkers. A subset of chemicals was also chosen based on that measured in Cycle 1 (2007–2009) of the Canadian Health Measures Survey [2] so that comparisons could be made to the general population biomonitoring data, given that measurements were made by the same laboratory. Only the persistent organic pollutants and PFASs measured in maternal and cord plasma are reported in this article. A total of 24 polychlorinated biphenyls (PCB 28, 52, 66, 74, 99, 101, 105, 118, 128, 138, 146, 153, 156, 163, 167, 170, 178, 180, 183, 187, 194, 201, 203 and 206), 14 organochlorinated pesticides (aldrin, beta-hexachlorocyclohexane (β-HCH), gamma-hexachlorocyclohexane (γ-HCH), hexachlorobenzene, cis-nonachlor, trans-nonachlor, α-chlordane, γ-chlordane, oxychlordane, dichlorodiphenyldichloroethylene (DDE), p,p’-dichlorodiphenyltrichloroethane (DDT), mirex, toxaphenes Parlar 26 and 50) and 9 polybrominated diphenyl ethers (PBDE 15, 17, 25, 28, 33, 47, 99, 100, 153) and hexabromobiphenyl (PBB 153) were measured by the Centre de Toxicologie du Québec (CTQ) of the Institut National de Santé Publique du Québec (INSPQ) in 1st trimester maternal plasma samples as well as cord plasma samples. The PFASs perfluorooctane sulfonate (PFOS), perfluorooctanoic acid (PFOA) and perfluorohexane sulfonate (PFHxS) were also measured in both 1st trimester maternal and cord plasma. For a subset of participants (n = 48) PFASs were also measured in the 3rd trimester.

Analytical methods

Two mL of plasma was enriched with labeled internal standards (PCB 141-13C12, PCB 153, -13C12, PCB 180-13C12, PCB 194-13C12, hexachlorobenzene-13C6, α-HCH-13C6, trans-nonachlor-13C10, oxychlordane-13C10, p,p’-DDE-13C12, Parlar 26-13C10, Parlar 50-13C10, PBDE-77-13C12) plus analogous internal standards (3,6-F2-PBDE 99, PBDE 101) and proteins were denaturated with reagent grade alcohol. POP compounds were extracted with hexane from the aqueous matrix using a liquid-liquid extraction in the presence of a saturated ammonium sulfate solution for salting out. Thereafter, the extracts were evaporated to dryness before they were redissolved in 0.5 mL of hexane. These extracts were further purified on activated florisil columns and which were eluted with a mixture of dichloromethane:hexane (9 mL; 25:75) prior to GC-MS analysis.

The solvent was then evaporated, the residual taken up in 20 μL of hexane and analyzed for POP compounds on an Agilent 6890 Network or 7890A gas chromatograph (GC) coupled to an Agilent 5973 Network or 5975C mass spectrometer (MS) (Agilent Technologies; Mississauga, Ontario, Canada). The GC was fitted with an Agilent 60 m DB-XLB column (0.25 mm i.d., 0.25 μm film thickness) for detection by MS and with an Agilent Ultra-1 50 m (0.20 mm i.d., 0.33 μm film thickness) (Agilent Technologies; Mississauga, Ontario, Canada) column for the Electron Capture Detector (ECD). The carrier gas was helium and the injections were 3 μL in splitless mode. The mass spectrometer was operated in selected ion monitoring (SIM) mode, using negative chemical ionization (NCI) with methane (99.97 %) as the reagent gas. The ECD serves only to quantify PCB congeners 28 and 52 when the detection limits for these compounds were not achieved with the mass detector.

Concentrations were reported in units of micrograms per liter (μg/L) and the limits of detection (LOD) were between 0.005 and 0.3 μg/L for POPs. LODs were determined by first estimating concentrations of analytes yielding a signal to noise ratio of 3. Plasma samples spiked with analytes in concentrations ranging from 4 to 10 times the estimated LODs were analyzed (10 replicates) and standard deviations were multiplied by three to obtain the LODs. The method recoveries for each analyte varied from 68 to 90 %. The intra-day precision (repeatability) and the inter-day precision (reproducibility) of the method were respectively between 1.2 to 8.3 % and 2.8 to 13 %. Total cholesterol (TC), free cholesterol (FC), triglycerides (TG) and phospholipids (PL) levels were also measured in these samples by enzymatic methods combined with colorimetry (in g/L) at the laboratory of Centre Hospitalier de l’Université Laval (CHUL; Quebec, Quebec) and used to calculate the total lipid level as 1.677*(TC-FC) + FC + TG + PL [38].

The PFAS analysis was performed as described in the Canadian Health Measures Survey (CHMS) Cycle 1 report [2]. The LODs were between 0.1 to 0.3 μg/L for the compounds PFHxS, PFOA and PFOS. The intra-day precision varied between 5.4 and 6.3 % and the inter-day precision varied between 4.9 and 10 %.

The internal reference materials used to control the quality of the analyses were the certified reference material SRM-1958 (POPs and PFASs) from the National Institute of Standards and Technology (NIST; Gaithersburg, MD), the reference materials W-09-02 and W-10-06 (POPs) from the External Quality Assessment Scheme within the Arctic Monitoring and Assessment Program (AMAP) (Centre de toxicologie du Québec (CTQ), Institut National de Santé Publique du Québec (INSPQ), Québec, Canada) and some in-house reference materials for PFASs.

The overall quality and accuracy for both analytical methods was monitored by participation in the interlaboratory program AMAP External Quality Assessment Scheme (Centre de toxicologie du Québec (CTQ), Institut National de Santé Publique du Québec (INSPQ), Québec, Canada) as well as the German External Quality Assessment Scheme (G-EQUAS; Erlangen, Germany).

Statistical analysis

As most contaminants had values below the limit of detection, censoring methods [39] were implemented for descriptive statistics, hypothesis tests and linear regressions. Such techniques are classified as either parametric methods, such as maximum likelihood (ML) estimation, or nonparametric methods, such as Kaplan-Meier (KM) and the generalized Wilcoxon test [39]. Total lipids were included in the models of all POPs other than the PFASs as a covariate.

Descriptive statistics including sample size, detection limit, percentage of observations below the limit of detection (LOD), minimum, median, 95th percentile, maximum, geometric mean, geometric standard error and associated 95 % confidence interval were reported for maternal and cord plasma concentrations of POPs, both adjusted and unadjusted for total lipids, with the exception of PFASs which were not lipid-adjusted. Note that the highest detection limit is presented in tables when several detection limits were noted.

For censoring methods, the geometric mean and 95 % confidence interval were calculated using the ML method and compared to the empirical median from the KM approach. The Greenwood estimate of variance was used for determination of Kaplan-Meier confidence intervals. Contaminants having the % < LOD of approximately 50 % were analyzed using the censored methods. Justification for including contaminants with up to 50 % censoring is provided in Helsel [39].

Demographic variables which were considered as potential predictors of contaminant concentrations, including parity, maternal age group (<25, 25–29, 30–34, 35+), smoking status (current, former, never), household income in Canadian dollars (≤$50,000, $50,001–$100,000, >$100,000), pre-pregnancy body mass index (BMI) based on self-reported pre-pregnancy weight and measured height and categorized as Underweight to Normal (BMI < 25); Overweight (25 < = BMI < 30); and Obese (BMI > =30), place of birth (foreign-born, Canadian born), fasting status (yes, no), maternal education (high school or less, some college or college degree, undergraduate degree or higher), sample collection year (2008–2011), consumption of: any kind of fish (never, 1, or 2+ times per week), bacon (never, 1, or 2+ times per week), hamburger (never, 1, 2, or >2 times per week), pork (never, 1, or 2+ times per week), poultry (never, 1, 2, or >2 times per week) and steak (never, 1, or 2+ times per week), use of non-stick cooking vessels (only for PFASs) and infant gender for cord plasma. Hypothesis tests were performed for contaminants with at least 50 % of observations above LOD [39] using the likelihood ratio test for parametric ML estimation and the nonparametric Wilcoxon rank-sum test. Bonferroni-adjusted confidence intervals were calculated and used to identify the different groups when overall tests were significant. To aid model selection, a test for log-normality with left-censored observations developed by Nysen et. al. [40] was used. If the assumption of normality failed, then nonparametric testing results were presented. Lipid adjusted models included total lipids of each sample as a covariate in the linear model with the potential predictor of interest.

In addition to performing the analysis described above, we also considered evaluation of infant cord plasma based on three demographic variables: infant gender, maternal smoking status and season of cord plasma collection. The maximum likelihood estimation (MLE) method was employed to account for left–censored repeated measures (twins and triplets), using nonlinear mixed models, analogous to Jin et. al. [41] and Thiebaut and Jacqmin-Gadda [42] which employed the NLMIXED procedure in SAS. Hypothesis testing was performed using likelihood ratio tests that followed a chi-square distribution.

Furthermore, prediction intervals were computed for geometric mean contaminant concentrations by the three demographic variables of interest, using Empirical Bayes estimates of the random effects [43]. Interpretations of these geometric means are similar to those computed for the previous models.

Linear associations among all unadjusted chemicals with >70 % detection were examined using the correlation coefficient. Spearman’s rho (ρ) was calculated since the contaminant concentrations were not normally distributed. Observations below the LOD were imputed by LOD/2. A heat map was plotted to represent Spearman correlation coefficient matrix.

For the 48 participants who had PFAS measurements in both the 1st and 3rd trimester we calculated intra-class correlation coefficients (ICCs). ICCs were calculated using a one-way random effects model (Proc Mixed) to estimate the between- and within-subject variability across both time points. The ICC measures the ratio of between-subject variance to total variance. It ranges from 0 to 1, with 0 meaning no within person reproducibility and 1 meaning perfect reproducibility.

Placental transfer was described by the calculation of the concentration ratios between paired cord and maternal samples for each compound on unadjusted and lipid adjusted concentrations (excluding the PFASs) using the formula Rcm = Cuc / Cm where Cuc is the umbilical cord concentration and Cm is the maternal concentration. Ratio calculations are only presented for those chemicals that had ≥10 pairs above the LOD [9].

Statistical analysis was performed using software packages SAS (Statistical Analysis System) Enterprise Guide 4.2 and R (R Core Development Team). For the censoring methods, functions from the R packages NADA and SURVIVAL were used for analysis. Unless otherwise indicated, a 5 % significance level (α = 0.05) was implemented throughout.

Results

We found high detection rates in maternal blood for a number of chemicals but limited detection in cord blood. The PFASs were found to be highly reproducible in a small subset of samples that had PFASs measured in the 1st and 3rd trimester. Associations were found between and number of covariates, including parity, maternal age, income, and fish consumption in line with other studies. Foreign born participants appear to have higher levels of some chemicals. The maternal:cord plasma ratios are described and all fall below 1.

There were a total of 1983 pregnant women in the MIREC study [37]. The mean maternal age was 32.2 years and most of the women were in their 1st or 2nd pregnancy. The vast majority were Canadian born (81.3 %) and married (71.8 %) and close to 60 % had at least one university degree. Only 12 % were current smokers, while 27 % were former smokers. The majority were in the normal pre-pregnancy BMI ranges, however more than a third were overweight or obese. There were a total of 1959 live births in the study and 1517 cord plasma samples were collected. There were 1934 singletons, and 49 multiple births. The infants were 53 % male and 47 % female (See Table 1).
Table 1

Study population

Characteristic

Frequency

Percent

Maternal age group

  

 <25

139

7.01

 25–29

459

23.15

 30–34

709

35.75

 35+

676

34.09

Smoking status

  

 Current

237

11.96

 Former

542

27.36

 Never

1202

60.68

Country of birth

  

 Foreign born

371

18.71

 Canadian born

1612

81.29

Maternal education

  

 High school or less

175

8.83

 Some college or college degree

572

28.87

 Undergraduate degree or higher

1234

62.29

Marital status

  

 Married

1424

71.81

 Other

559

28.19

Income

  

 ≤$50,000

347

17.49

 $50,001–$100,000

786

39.64

 More than $100,000

757

38.17

Parity

  

 0

874

44.12

 1

800

40.38

 2+

307

15.5

Body mass index (BMI)

  

 Underweight to normal (BMI <25)

1164

63.36

 Overweight (25 ≤ BMI <30)

404

21.99

 Obese (BMI >30)

269

14.64

Fasting status

  

 No

1914

98

 Yes

39

2

Season of sampling (1st trimester)

  

 Fall

575

29.41

 Spring

448

22.92

 Summer

464

23.73

 Winter

468

23.94

Infant gender

  

 Male

1034

52.51

 Female

926

47.03

Babies

  

 Singletons

1934

97.53

 Twins

47

2.37

 Triplets

2

0.10

Note: for income and infant gender, sum of percent is not 100, because there is a group (don’t know) was not included

Tables 2, 3, 4, 5, 6 and 7 report the overall summary statistics for each contaminant. In Table 2, the highest PFAS geometric mean (GM) in maternal plasma was PFOS (4.56 μg/L). PFOA, PFOS and PFHxS were detected in 23–64 % of the cord plasma. The GM of maternal PFOA was 4 times higher than that of cord plasma (1.65 vs 0.35 μg/L). There was a moderate and positive linear association among all the PFASs in maternal plasma (See Table 3). There was also a significant and positive correlation between maternal and cord plasma for PFOA.
Table 2

Descriptive statistics for PFASs in maternal and cord blood plasma (wet weight—μg/L)

Contaminant

Aliquot

N

LOD

% < LOD

Min

Median

95th Percentile

Max

KM Median

95 % CI

GM MLE

95 % CI

PFHxS

Maternal

1940

0.3

5.31

ND

1

4.3

40

1

0.96

1.05

1.03

0.99

1.07

Cord

1385

0.3

77.11

ND

ND

0.626

1.9

NA

NA

NA

NA

NA

NA

PFOA

Maternal

1940

0.1

0.15

ND

1.7

4.1

16

1.7

1.65

1.75

1.65

1.60

1.69

Cord

1384

0.3

36.42

ND

0.39

1.1

5.6

0.39

0.37

0.41

0.35

0.33

0.36

PFOS

Maternal

1940

0.3

0.15

ND

4.6

11

36

4.6

4.47

4.73

4.56

4.45

4.68

Cord

1385

0.3

52.27

ND

ND

1.5

5.8

NA

NA

NA

NA

NA

NA

ND Non-detects (value below the limit of detection)

NA Non-applicable (KM median and GM MLE of contaminants with less than 50 % of observations detected were not calculated)

Table 3

Correlations among PFOA, PFOS and PFHxS

Maternal plasma (1st trimester)

Spearman correlation

Maternal (1st trimester): Cord Plasma

Spearman correlation

PFOA: PFOS

0.56

PFOA: PFOA

0.67

PFOA: PFHxS

0.50

  

PFOS: PFHxS

0.53

  

Correlations between maternal and cord blood for PFOS and PFHxS not presented since more than 70 % of the observations were undetected

Table 4

Comparison of 1st trimester and 3rd trimester PFAS concentrations

 

% below LOD

1st trimester GM

3rd trimester GM

ICC

Spearman correlation

PFOA

0

1.71

1.06

0.64 (0.46, 0.78)

0.90

PFOS

0

5.70

3.78

0.69 (0.53, 0.82)

0.91

PFHxS

5

0.98

0.70

0.83 (0.73, 0.90)

0.98

N = 48 paired samples measured in both the 1st and 3rd trimester of pregnancy

Table 5

Descriptive statistics for MIREC PCBs concentrations in maternal and cord blood plasma (lipid-adjusted—μg/kg)

Contaminanta

Aliquot

N

LOD

% < LOD

Min

Median

95th Percentile

Max

KM Median

95 % CI

GM

95 % CI

Mono-ortho Dioxin-Like PCBs

 PCB105

Maternal

1935

0.01

95.71

ND

ND

ND

13.62

NA

NA

NA

NA

NA

NA

Cord

1382

0.01

99.86

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB118

Maternal

1935

0.01

26.61

ND

2.33

6.78

37.93

2.30

2.22

2.37

2.36

2.29

2.43

Cord

1382

0.01

98.34

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB156

Maternal

1935

0.01

79.07

ND

ND

3.52

17.46

NA

NA

NA

NA

NA

NA

Cord

1380

0.01

99.71

ND

ND

ND

100.00

NA

NA

NA

NA

NA

NA

 PCB167

Maternal

1935

0.01

98.40

ND

ND

ND

4.49

NA

NA

NA

NA

NA

NA

Non-dioxin-like PCBs

 PCB28

Maternal

1934

0.05

99.74

ND

ND

ND

260

NA

NA

NA

NA

NA

NA

 PCB66

Maternal

1934

0.03

99.28

ND

ND

ND

28

NA

NA

NA

NA

NA

NA

 PCB74

Maternal

1935

0.03

96.54

ND

ND

ND

18.4

NA

NA

NA

NA

NA

NA

 PCB99

Maternal

1934

0.03

97.16

ND

ND

ND

12.93

NA

NA

NA

NA

NA

NA

 PCB101

Maternal

1934

0.03

99.90

ND

ND

ND

12.07

NA

NA

NA

NA

NA

NA

 PCB128

Maternal

1935

0.01

99.79

ND

ND

ND

5

NA

NA

NA

NA

NA

NA

 PCB138

Maternal

1935

0.01

7.03

ND

4.07

14.77

71.67

4.07

3.91

4.23

4.21

4.08

4.35

Cord

1382

0.01

95.08

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB146

Maternal

1935

0.01

85.43

ND

ND

2.93

16

NA

NA

NA

NA

NA

NA

Cord

1382

0.01

99.86

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB153

Maternal

1935

0.01

1.29

ND

7

25.95

155

7

6.73

7.27

7.30

7.07

7.54

Cord

1382

0.01

84.01

ND

ND

45.26

101.45

NA

NA

NA

NA

NA

NA

 PCB170

Maternal

1935

0.01

46.82

ND

2

7.22

71.67

1.69

1.62

1.76

1.67

1.59

1.75

Cord

1382

0.01

98.34

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB163

Maternal

1935

0.01

68.11

ND

ND

4.70

23.81

NA

NA

NA

NA

NA

NA

Cord

1382

0.01

99.20

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB178

Maternal

1935

0.01

95.71

ND

ND

ND

9.02

NA

NA

NA

NA

NA

NA

 PCB180

Maternal

1935

0.01

7.39

ND

4.72

19.70

183.33

4.72

4.53

4.91

4.88

4.70

5.06

Cord

1382

0.01

93.63

ND

ND

41.67

100

NA

NA

NA

NA

NA

NA

 PCB183

Maternal

1935

0.01

91.21

ND

ND

2.50

23.33

NA

NA

NA

NA

NA

NA

Cord

1382

0.01

99.93

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB187

Maternal

1935

0.01

57.21

ND

ND

5.88

45

NA

NA

NA

NA

NA

NA

Cord

1382

0.01

99.57

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB194

Maternal

1928

0.01

81.17

ND

ND

3.39

30

NA

NA

NA

NA

NA

NA

Cord

1382

0.01

99.93

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

 PCB201

Maternal

1935

0.01

83.72

ND

ND

2.97

20

NA

NA

NA

NA

NA

NA

 PCB203

Maternal

1935

0.01

89.35

ND

ND

2.56

14.17

NA

NA

NA

NA

NA

NA

 PCB206

Maternal

1928

0.01

97.67

ND

ND

ND

6.61

NA

NA

NA

NA

NA

NA

ND Due to a high percentage of non-detects, descriptive statistics were not reported

NA Non-applicable (KM median and GM MLE of contaminants with less than 50 % of observations detected were not calculated)

a Contaminants PCB 52 was not detected in both maternal and cord blood samples. Contaminants PCB 101, PCB 128, PCB 167, PCB 178, PCB 201, PCB 203, PCB 206, PCB 28, PCB 66, PCB 74, PCB 99, were not detected in the cord blood

Table 6

Descriptive statistics for MIREC Organochorine concentrations in maternal and cord blood plasma (lipid-adjusted—μg/kg)

Contaminanta

Aliquot

N

LOD

% < LOD

Min

Median

95th Percentile

Max

KM Median

95 % CI

GM

95 % CI

Beta-HCH

Maternal

1898

0.01

31.88

ND

2.31

18.97

1108.11

2.24

2.15

2.32

2.32

2.19

2.46

Cord

1379

0.01

93.55

ND

ND

47.62

740.74

NA

NA

NA

NA

NA

NA

Cis-nonachlor

Maternal

1934

0.005

88.31

ND

ND

1.25

3.91

NA

NA

NA

NA

NA

NA

DDE

Maternal

1935

0.09

1.03

ND

48.33

262.55

5306.12

48.33

46.68

49.99

56.02

54.02

58.08

Cord

1382

0.09

87.48

ND

ND

452.50

1827.96

NA

NA

NA

NA

NA

NA

DDT

Maternal

1935

0.05

96.28

ND

ND

ND

175.44

NA

NA

NA

NA

NA

NA

Cord

1381

0.05

99.71

ND

ND

ND

500

NA

NA

NA

NA

NA

NA

HCB

Maternal

1934

0.04

69.54

ND

ND

11.73

101.67

NA

NA

NA

NA

NA

NA

Cord

1380

0.04

99.86

ND

ND

ND

400

NA

NA

NA

NA

NA

NA

Mirex

Maternal

1934

0.01

91.83

ND

ND

2.50

38.03

NA

NA

NA

NA

NA

NA

Oxychlordane

Maternal

1933

0.005

7.81

ND

2.09

4.60

17.5

2.09

2.02

2.15

2.01

1.96

2.06

Cord

1378

0.005

97.97

ND

ND

ND

50

NA

NA

NA

NA

NA

NA

Parlar26

Maternal

1934

0.005

97.47

ND

ND

ND

3.65

NA

NA

NA

NA

NA

NA

Parlar50

Maternal

1934

0.005

87.28

ND

ND

1.22

5

NA

NA

NA

NA

NA

NA

Transnonachlor

Maternal

1934

0.01

15.87

ND

2.89

7.30

34.33

2.88

2.78

2.99

2.90

2.83

2.98

Cord

1381

0.01

98.99

ND

ND

ND

100

NA

NA

NA

NA

NA

NA

ND Due to a high percentage of non-detects, descriptive statistics were not reported

NA Non-applicable (KM median and GM MLE of contaminants with less than 50 % of observations detected were not calculated)

a Aldrin, Alpha-chlordane, Gamma-Chlordane, and Gamma-HCH were not detected in both maternal and cord blood samples. Contaminants cis-nonachlor, Mirex, Parlar-26, and Parlar-50 were not detected in the cord blood

Table 7

Descriptive statistics for MIREC PBB and PBDEs concentrations in maternal and cord blood plasma (lipid-adjusted—μg/kg)

Contaminanta

Aliquot

N

LOD

% < LOD

Min

Median

95th Percentile

Max

KM Median

95 % CI

GM

95 % CI

PBB153

Maternal

1928

0.02

99.48

ND

ND

ND

13.62

NA

NA

NA

NA

NA

NA

PBDE100

Maternal

1927

0.02

78.46

ND

ND

10.16

327.27

NA

NA

NA

NA

NA

NA

Cord

1379

0.02

99.06

ND

ND

ND

200

NA

NA

NA

NA

NA

NA

PBDE153

Maternal

1928

0.02

55.60

ND

ND

36.36

527.27

NA

NA

NA

NA

NA

NA

Cord

1381

0.02

96.96

ND

ND

ND

221.05

NA

NA

NA

NA

NA

NA

PBDE28

Maternal

1928

0.03

99.07

ND

ND

ND

27.14

NA

NA

NA

NA

NA

NA

PBDE33

Maternal

1927

0.03

99.90

ND

ND

ND

8.57

NA

NA

NA

NA

NA

NA

PBDE47

Maternal

1928

0.03

34.28

ND

7.19

37.78

727.27

7.00

6.65

7.35

7.02

6.68

7.38

Cord

1379

0.03

94.63

ND

ND

125

411.76

NA

NA

NA

NA

NA

NA

PBDE99

Maternal

1927

0.02

80.85

ND

ND

8.36

169.09

NA

NA

NA

NA

NA

NA

Cord

1379

0.02

98.55

ND

ND

ND

1148.15

NA

NA

NA

NA

NA

NA

ND Due to a high percentage of non-detects, descriptive statistics were not reported

NA Non-applicable (KM median and GM MLE of contaminants with less than 50 % of observations detected were not calculated)

a PBDE 15, PBDE 17, and PBDE 25 were not detected in both maternal and cord blood samples. PBB 153, PBDE 28, PBDE 33, were not detected in the cord blood

Table 4 describes the correlation between the paired 1st and 3rd trimester PFAS concentrations for a subset of women who had them measured at both time points. The 1st and 3rd trimester samples were highly correlated and had moderate to high reproducibility with ICCs ranging from 0.6 to 0.8. The 1st trimester samples were consistently higher than the 3rd trimester samples. The PCBs 118, 138, 153, and180 were the most highly detected PCBs (Table 5). DDE and oxychlordane were the most highly detected organochlorines (Table 6) while PBDE47 was the most highly detected flame retardant (See Table 7). Certain contaminants, namely aldrin, α-chlordane, γ-chlordane, γ-HCH, PBDE 15, PBDE 17, PBDE 25 and PCB 52 were not detected in either maternal or cord plasma samples. Cord plasma concentrations were very low or not detected for most of the PCBs and PBDEs.

In Table 8 we present the median cord:maternal plasma concentration ratios. The unadjusted median ratios (0.08–0.28) are much lower than the lipid adjusted (0.60–0.87).
Table 8

Cord-maternal plasma median concentration ratios (Cm = Cuc / Cm)

 

MIREC (plasma)

Vizcaino et al. 2014 [9] (serum)

Needham et al. 2011 [70] (serum)

Chemical

No. of pairs

Median

Median lipid adjusted

Median

Median lipid adjusted

Median

Beta-HCH

88

0.16

0.78

0.34

0.70

 

DDE

168

0.15

0.74

0.34

0.68

 

Oxychlordane

28

0.21

0.87

   

PBDE100

12

0.08

0.60

   

PBDE153

40

0.10

0.48

0.31

0.58

0.34a

PBDE47

67

0.15

0.84

0.58

0.90

 

PCB118

23

0.21

0.80

0.45

0.98

 

PCB138

67

0.16

0.70

0.39

0.81

 

PCB153

215

0.14

0.72

0.37

0.75

 

PCB163

11

0.23

0.80

   

PCB170

23

0.14

0.71

   

PCB180

86

0.13

0.67

0.28

0.57

 

Transnonachlor

14

0.19

0.79

   

PFHxS

315

0.23

   

0.74

PFOA

865

0.28

   

0.72

PFOS

648

0.14

   

0.34

Note: only chemicals with >10 pairs shown (where both the maternal and cord blood concentrations were above the LOD)

amean

Note that these ratios are only presented for pairs of maternal and cord plasma samples that are both above the LOD. The highest number of pairs was for PFOA (n = 865) while the highest median ratios (lipid adjusted) were for oxychlordane and PBDE47.

The median number of POPs detected in maternal plasma above the LOD was 14 (mean 15) with a maximum of 33. In cord plasma, very few chemicals were detected with a mean and median of 2 chemicals per cord plasma sample and a maximum of 19 chemicals. Figure 1 describes the correlation across chemicals in maternal plasma for those chemicals with >70 % above the LOD. The organochorine pesticides and PCBs showed moderate to high correlation with each other but low correlation with the PFASs. The PFASs were moderately correlated with each other.
Fig. 1
Fig. 1

Correlation Heat Map (Maternal Plasma). All chemicals with >70 % detection

Demographic variables were explored for contaminants having at least 50 % of the observations above the LOD and included: β-HCH, DDE, oxychlordane, PBDE153, PBDE47, PCB118, PCB138, PCB153, PCB180, trans-nonachlor, PFHxS, PFOA, and PFOS. Sufficient detection permitted consideration of PCB 170 levels by parity and place of birth only (See Table 9 for summary and Additional file 1 for further details).
Table 9

Hypothesis testing summary

 

Beta-HCH

DDE

Oxychlordane

PBDE47

PCB118

PCB138

PCB153

PCB180

Transnonachlor

PFHxS

PFOA

PFOS

Increasing parity

-

-

-

NS

-

-

-

NS*

-

-

-

-

Increasing maternal age

NA

+

+

NS*

NA

+

+

+

NA

-

-

NS*

Current smokers

-

-

-

NS*

-

-

+

-

-

NS*

-

NS*

High household income > $100,000 CDN

+

NS*

+

NS*

+

+

+

+

+

NS*

+

+

High pre-pregnancy BMI

+

-

-

+

-

-

-

-

-

NS*

NS

NS

Foreign born

+

+

+

-

+

+

+

+

+

-

NS

-

Fasting at time of sample

NS

-

-

NS

NS

-

NS

NS

-

NS

NS

NS

Lower maternal education

-

-

-

NS*

-

-

-

-

-

NS

NS*

-

Sampling year (2011 vs 2008)

NA

-

-

-

-

-

-

-

-

NS

-

-

Fish consumption

+

+

+

NS*

+

+

+

+

+

NS

NS

NS

Bacon consumption

NA*

-

NS

NA*

NS*

NS

NS

NS

NS

NS

NS

NS

Hamburger consumption

-

-

NS*

NS

-

-

-

-

NS*

NS

NS

NS

Pork consumption

NS

NS

NS

NS

NS

NS

NS

NS

NS

NS

NS

NS

Poultry consumption

NS

NS

NS*

NS

NS*

NS

NS*

NS*

NS

NS

NS

NS

Steak consumption

NS

NS

NS

NS

NS

NS

NS

NS

NS

NS

NS

NS

Cook with non-stick cooking vessels

         

NS

+

NS

NA = not sufficient detection (>70 % below LOD) in categories for analysis

NA* = significant interaction with chemical and lipids. See Additional file 1 for details

NS = No statistically significant differences between groups

NS* = overall a significant effect was seen for this characteristic (i.e. parity, maternal age, smoking status, income, BMI, education level) but the test could not identify with sufficient confidence which pairs of means differ. The Bonferroni-adjusted confidence intervals are a very conservative method

- means a significant negative association (e.g. as parity increases DDE concentrations decrease)

+ means a significant positive association (e.g. as maternal age increases DDE concentrations increase)

Significant differences in contaminant concentrations were found by parity group for all contaminants considered except PBDE 47, with and without lipid adjustment. Generally, as the parity increases, the contaminant concentrations tended to decrease. We saw that contaminant levels were significantly higher in the older participants for the contaminants DDE, oxychlordane, PCB 138, PCB 153, and PCB180. However for two of the PFASs, the age group 35+ had significantly lower concentrations of PFHxS and PFOA than the younger age groups.

There were significant differences by smoking status for all contaminants considered with and without lipid adjustment except for PFOS. In general, non-smokers and former smokers had higher contaminant concentrations compared to current smokers. Only PBDE153 had higher concentrations in current smokers than non-smokers.

For household income we saw significant differences with and without lipid adjustment. Generally, as household income increased, the contaminant concentrations tended to increase in many cases, hence mothers with a household income of more than $100,000 CDN had significantly higher contaminant residue levels.

The majority of the lipid adjusted contaminants had significantly higher concentrations in underweight/normal weight mothers compared to obese mothers. However, there was an exception for β-HCH and PBDE-47, where significantly higher concentrations were seen for obese women in most cases.

Contaminant concentrations were significantly higher (unadjusted and lipid adjusted) in foreign-born mothers compared to Canadian-born mothers for all contaminants except PBDE 47 and the PFASs (PFHxS and PFOS), where higher concentrations were seen in Canadian-born mothers.

Fasting status demonstrated significant differences for DDE, oxychlordane, PCB 138 and trans-nonachlor with and without lipid adjustment. Contaminant residue levels were higher among those mothers who did not fast. For the other chemicals, no significant difference at the 5 % significance level was found with lipid adjustment.

There were significant differences by education level for nearly all contaminants. Generally, mothers with higher education had higher contaminant concentrations. Sampling year showed a significant effect for nearly all POPs. Further to this, women who participated in the study in 2011 had significantly lower concentrations of nearly all POPs compared to women who participated in 2008.

Fish consumers had significantly higher levels of nearly all POPs excluding the PFASs. Bacon, pork, poultry and steak consumption showed little effect on contaminant concentrations however participants who ate hamburger 2 or more times per week showed significantly lower levels of the OC pesticides β-HCH, DDE, and the PCBs (PCBs 118, 138, 153, 180). Only PFOA levels were higher for participants who cooked with non-stick cooking vessels. However no association was observed if they microwaved with non-stick cooking vessels.

No significant differences were detected when grouping by infant gender, maternal smoking status or season of collection for PFOA in cord plasma (See Additional file 1).

Discussion

In maternal plasma, there was >90 % detection for DDE, oxychlordane, PCB 138, PCB 153, and the PFASs. Cord plasma had much lower detection rates with low or very limited detection for most PCBs and PBDEs. The highest detection rate in cord plasma was for the PFASs at 23 (PFHxS), 48 (PFOS) and 64 (PFOS) percent. In a small subsample we found maternal plasma PFASs concentrations to be highly correlated and to have good reproducibility between the 1st and 3rd trimester (ICCs 064-0.83). The cord:maternal plasma concentration ratios ranged from 0.14 (PFOS) to 0.87 (oxychlordane, lipid adjusted). Similar to other studies, we found parity, maternal age, income, education, smoking status, pre-pregnancy BMI and fish consumption to be significant predictors for most chemicals. Those participants who were foreign-born had significantly higher concentrations of organochlorinated pesticides and PCBs.

In comparison to other national surveys, the participants of the MIREC cohort had lower geometric mean concentrations of DDE. MIREC’s DDE concentrations were lower than those measured in females from the population-based Canadian Health Measures Survey (CHMS) [2] as well as females [4] and pregnant women [44] from the U.S. National Health And Nutrition Examination Survey (NHANES) study. Maternal trans-nonachlor and oxychlordane concentrations appear to be similar in MIREC to those found in the CHMS [2] and another Canadian study [45], and lower than that found in NHANES. The predominant PCB congeners were 138, 153, and 180 in the MIREC maternal plasma samples. This is consistent with other biomonitoring surveys in Canada [46]. Among the dioxin-like PCBs measured in MIREC, only PCB 118 was consistently detected in maternal plasma. PCB 118 concentrations were similar to those found in the CHMS [2] however, lower than other similar studies [4, 34, 45, 47, 72]. In cord plasma PCBs were rarely detected.

In the MIREC study cord plasma, the PFASs were detected more frequently than any other POPs. PFOA and PFOS had detection rates of 64 and 48 %, which is in contrast to the OC pesticides and PCBs that had only a 7–15 % detection rate. The 1st and 3rd trimester PFASs were found to be strongly correlated and moderately to strongly reproducible, with 1st trimester levels consistently higher, and ICCs ranging from 0.64 (PFOA) to 0.83 (PFHxS). Fei et al. [48] also found a high degree of correlation between 1st and 2nd trimester concentration of PFOA (r = 0.88) and PFOS (r = 0.87), with mean levels being higher in the 1st trimester. The MIREC maternal PFASs concentrations were similar to those found in females aged 20–39 in the population based study CHMS and another Canadian pregnancy cohort study based in Vancouver (CHiRP) [49] both conducted around the same time as MIREC. The MIREC PFOA and PFOS maternal concentrations are lower than those observed in earlier studies from the U.S. [3, 44], Norway [50], Denmark [51] and the Family study [52] from Hamilton, Ontario Canada. Cord plasma PFOA was significantly correlated with maternal plasma concentrations (p < 0.0001), as seen in other studies [8]. The MIREC PFOA cord plasma concentrations are also lower than those seen in other Canadian, and international studies, but similar to those reported in the Norwegian Birth Cohort (MoBa) [53].

PBDE 47 was the most frequently detected PBDE in the MIREC study. However, the MIREC PBDE 47 concentrations are notably lower than those found in earlier studies of pregnant women [44] and females [4] from the U.S. NHANES study and the Family study from Hamilton, Ontario [54]. Concentrations are similar to that found in the CHMS [2], conducted at the same time as MIREC, and the Canadian centres of an earlier Trinational study [45].

Parity, maternal age, income, education, smoking status, pre-pregnancy BMI, year of collection and fish consumption were found to be significant predictors for most chemicals. Foreign Born participants had higher levels of PCBs and organochlorinated pesticides.

Generally, as parity increases contaminant concentrations tended to decrease. The organochlorinated concentrations were significantly higher in older age groups, except the PFASs where both PFHxS and PFOA had lower concentrations in older mothers. Fei et al. [48, 51] also found declining PFASs concentrations with increasing age. In MIREC, obese participants had lower concentrations of DDE, oxychlordane, and the PCBs, and higher concentrations of β-HCH, and PBDE 47 compared to other lower weight categories. Other studies have shown lower PCB concentrations with increasing BMI [55] or no association with BMI [56].

Most contaminants were found to be higher in non-smokers and former smokers than current smokers, except for PFOS. This is in contrast to the findings in other studies which have shown a positive association with smoking and POP concentrations [5761] or show no difference by smoking status for DDE [55], PCBs [55], and PFASs [50]. Our finding may be due to unmeasured confounders given we looked at the characteristics univariately. However results from Ayotte et al. [62] suggested that smoking induces liver CYP1A2 activity, which alters porphyrin metabolism and increases the biotransformation of mono-ortho PCBs.

OCs are highly lipophilic and partition among various tissues depending on their lipid content. Phillips et al. [63] showed increases of 20 % in PCB, HCB and DDE concentrations in 20 adults following a meal. However, they found no difference when concentrations were lipid adjusted. In the MIREC study, the few participants who fasted (n = 39) had significantly lower OC concentrations (DDE, oxychlordane, PCB 138 and trans-nonachlor) with and without lipid adjustment, suggesting that lipid adjustment alone may be insufficient to account for postprandial changes in these contaminant concentrations in pregnant women and other confounding measures must be considered.

Foreign-born participants had significantly higher concentrations of organochlorinated pesticides and PCBs. Foreign born participants were mainly from Europe (35 %) and Asia (19 %), followed by the Caribbean, South America and the U.S (all 9 %), Africa (8 %), Middle East (7 %) and Oceania (1 %). A Trinational Biomonitoring study [45] also showed consistently higher concentrations in Canadian immigrants than in Canadian born participants. Curren et al. [64] found that foreign-born Canadians had higher concentrations of DDE and β-HCH compared to Canadian-born and Inuit mothers. These exposures may originate from imported foods or exposures that occurred outside of Canada [65] or it may be due to different cultural habits and lifestyles related to their country of origin.

Both fish and hamburger consumption showed significant effects on contaminant concentrations albeit in different directions. Fish consumers had significantly higher levels of most POPs (excluding the PFASs). Fish consumption is known to affect the levels of POPs [6668]. Hamburger consumption had a significant negative effect on POP levels. This finding is not supported in the literature as several studies have reported POPs in meat [69] and may reflect the fact that these participants are less likely to eat fish, where we saw a strong association with POPs. Among the women who reported eating hamburger 2 or more times per week, 60 % reported never eating fish.

We found that the year of the sample collection had a significant effect on POP concentrations. Lower levels were seen in 2011 compared to 2008 for nearly all POPs except PFHxS. This could reflect the fact that POP levels are decreasing over time as a result of bans. It may also reflect a difference in recruitment methods over time (e.g. older moms) and should be noted as an important consideration in cohort studies collecting data over a number of years.

The lipid adjusted cord:maternal serum concentration ratios for the OC pesticides, PBDEs and PCBs are all less than 1 and similar to a recent study from Spain [9] which analyzed samples from 308 mother-cord plasma pairs between 2004-08 (See Table 8). For the PFASs, PFOA had the highest median ratio (0.28) but is much lower than in a study of 15 women from a Faroe Islands fishing community where elevated exposures to marine contaminants occur [70]. It has been suggested that pollutant properties may affect the transport of pollutants from the mother to the fetus however Vizcaino et al. [9] did not show any correlation with pollutant properties such as molecular weight, molar volume, number of halogen substituents or log octanol water partition coefficient (Kow) and concentration ratios. Further exploration into the predictors of the maternal:fetal concentration ratio is warranted.

An examination of the chemicals measured in the serum of the pregnant women shows that most women had multiple PCBs, PBDEs and PFASs detected in their plasma. This result is supported by the work by Woodruff et al. [44] who showed that each pregnant woman in the NHANES study had at least 2 OC pesticides, one PBDE, two PFASs and four phthalates. Traditionally research has focused on single chemicals in the exposure assessment; however, there is growing recognition of the need to better assess the risk of mixtures and to understand the cumulative effects of multiple exposures and stressors [71].

One limitation and possible reason for lower concentrations in pregnant women compared to non-pregnant females in the CHMS is that we did not adjust for albumin. Albumin measurements can be used as a surrogate for plasma volume expansion in pregnancy. This plasma volume expansion may dilute environmental chemical concentrations in the plasma [44, 72]. Woodruff et al. [44] found that adjusting for albumin generally increased the GM estimates of persistent compounds (e.g. DDE) but not for non-persistent compounds. However, they suggest that the role of albumin as a transport protein during pregnancy requires further investigation. MIREC was also based on a convenience sample and is therefore not population-based and representative. Our results may also be biased towards women with higher age at delivery, education and income [37].

Conclusions

Multiple chemicals were detectable in the serum of the pregnant women in our study cohort, however the concentrations were much lower than those seen in other studies. We found parity, maternal age, income, education, smoking status, pre-pregnancy BMI, fish consumption and year of collection to be significant predictors for most chemicals. Foreign-born participants had significantly higher concentrations of OCs and PCBs. In maternal plasma the highest detection rates were seen for the PFOS, PFOA, DDE, and PCB153. However in cord plasma, PFOA had the highest detection rate. In a small subset of participants we found the PFASs maternal plasma concentrations to be highly correlated and to have moderate to high reproducibility between the 1st and 3rd trimester.

Abbreviations

BMI: 

body mass index

CHMS: 

Canadian Health Measures Survey

CTQ: 

Centre de Toxicologie du Québec

DDE: 

dichlorodiphenyldichloroethylene

DDT: 

p,p’-Dichlorodiphenyltrichloroethane

HCB: 

hexachlorobenzene

INSPQ: 

Institute National de Santé Publique

KM: 

Kaplan-Meier

LOD: 

limit of detection

MIREC: 

maternal-infant research on environmental chemicals

ML: 

maximum likelihood

MLE: 

maximum likelihood estimation

OCs: 

organochlorines

PBDEs: 

polybrominated diphenyl ethers

PCB: 

polychlorinated biphenyls

PFASs: 

perfluoroalkyl substances

PFASs: 

perfluoroalkyl substances

PFHxS: 

perfluorohexane sulfonate

PFOA: 

perfluorooctanoic acid

PFOS: 

perfluoroctane sulfonate

POPs: 

persistent organic pollutants

Tox 26: 

toxaphene parlar 26

Tox50: 

toxaphene parlar 50

β-HCH: 

β-Hexachlorocylcohexane

γ-HCH: 

γ-Hexachlorocylcohexane

Declarations

Acknowledgements

We would like to sincerely thank the participants of the MIREC study for their contributions to the study. We greatly value the hard work and dedication of the Study Coordinating Centre, Site Staff and the MIREC Study Group. This study was funded by Health Canada’s Chemicals Management Plan, the Ontario Ministry of the Environment and the Canadian Institute for Health Research (MOP-81285).

Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made. The Creative Commons Public Domain Dedication waiver (http://creativecommons.org/publicdomain/zero/1.0/) applies to the data made available in this article, unless otherwise stated.

Authors’ Affiliations

(1)
Healthy Environments and Consumer Safety Branch, Health Canada, Ottawa, ON, Canada
(2)
Le Centre de toxicologie du Québec, Institut nationale de santé publique du Québec, Québec, QC, Canada
(3)
Department of Obstetrics and Gynecology, Division of Reproductive Biology, McMaster University, Hamilton, ON, Canada
(4)
Centre hospitalier universitaire de Sherbrook (CHUS), Sherbrooke, QC, Canada
(5)
Population Studies Division, Environmental Health Science and Research Bureau, Environmental and Radiation Health Sciences Directorate, Health Canada, 50 Columbine Driveway, Tunney’s Pasture, Ottawa, AL 0801A K1A 0K9, Canada

References

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