1. Introduction
Thyroid hormone is fundamental for fetal development of all organs, including endocrine hormone changes in uterus. Some endocrine disruptor chemicals (EDCs) have been reported to have a possible effect on thyroid hormone homeostasis in newborns, such as polychlorinated biphenyl (PCB), or polybrominated diphenyl ethers [1,2,3], persistent organic pollutants (POP) [4] and bisphenols [5]. Permanent effects of thyroxin-related development, like on neurons in the brain, in infants and in later childhood are observed clinically where hypothyroidism of pregnant women occurred during pregnancy [6,7,8,9,10,11,12]. Previous studies had revealed possible effects on thyroid hormone homeostasis while exposed to certain phthalates in pregnant women [13,14,15]. A few studies reported the adverse or positive relationship between levels of cord serum phthalate metabolite and cord serum thyroid hormone (e.g., TSH and thyroxine) [15,16,17], however, whether phthalate exposure in the uterus can cause thyroid hormone alterations in newborns was debatable due to limitations such as small sample size, spot urine or serum sample, different phthalates or thyroid hormones observed, etc.
Phthalates are ubiquitous in daily life. They are added to plastics and many other daily products [18,19]. From 2003 to 2007, an average of 200,000 tons of di (2-ethylhexyl)phthalate (DEHP) and 20,000 tons of dibutyl phthalate (DBP) were used to produce consumer products in Taiwan [20]. Although phthalates are metabolized to their metabolites within a few hours or days [21], the potential consequences of human exposure to phthalates have focused on susceptible subjects, like pregnant women and fetuses [22,23,24,25,26,27,28]. Phthalate metabolites are considered to be good biomarkers for evaluating phthalate exposure in humans because of their low contamination rate in the laboratory and reliability for indicating an individual’s phthalate exposure [18,21,29]. In addition, animal and epidemiological studies have reported that phthalate metabolites can penetrate the placenta and be retained in the fetus [14,30,31,32]. Biomarkers of phthalates in different specimens were used to assess the exposure of early life in the uterus, such as meocoin, serum, and amniotic fluid samples [14,21,33].
Phthalates have also been suggested as having a possible antagonistic effect on thyroid functions [34,35,36,37,38,39,40] and may alter thyroid hormone through the oxidative stress pathway [19,41,42]. This may be relevant to other environmental disrupter compounds [1,40,43,44]. Though several epidemiological studies have investigated the association between phthalate metabolites and maternal and cord serum thyroid hormones, there were inconsistencies in the observed results of specific phthalates and the alterations of the phthalate-thyroid hormone relationships [16,17,45,46,47]. Furthermore, little is known about the maternal phthalate metabolites in urine, serum and cord blood samples at delivery, in relation to maternal serum and cord serum thyroid hormones.
Therefore, the aims of this study are to investigate the relationship between phthalate metabolites and thyroid hormones in cord serum and maternal serum samples using the existing cohort we established.
2. Material and Method
2.1. Participants
Participants of this study were recruited from a cohort for evaluating prenatal phthalates exposure (during the third trimester) to the pregnant women and newborns during 2005 to 2006 [13]. All participants were interviewed and the benefits and risks of participating in this longitudinal project were fully explained. Of all participants who signed the informed consent for this study, 76 pregnant women received follow-up, and urine, serum and cord blood samples were collected in 61 of them. All samples were collected in the third trimester before delivery. The protocol was approved by the Human Ethics Committee of the National Cheng Kung University Hospital.
2.2. Samples Collection
Urine samples of 20–30 mL were collected using 250 mL glass vessels and the urine samples were immediately transferred into 12 mL amber glass bottles for phthalate monoester and creatinine analysis. All urine samples were stored at −20 °C until analysis. Meanwhile, we drew 8 mL blood samples via venipuncture into chemically clean glass tubes containing no anti-coagulant. After delivery, cord blood samples were drawn by gynecologists using 20-mL glass syringe and transferred into chemically clean glass tubes. Maternal and cord blood were centrifuged at 2500 rpm in 45 min to obtain serum samples and stored at −70 °C in amber glass bottles until analysis. To prevent possible contamination of the urine and serum samples, all the glassware had been washed in methanol, acetonitrile and acetone, and then was sealed with aluminum foil before sample collection. Glass syringes were sterilized with ethylene oxide for the cord blood sample collection. We used 5 mL of HPLC-grade H2O to extract all the glassware, and it was analyzed to ensure no phthalate metabolites contamination during the preparation of the glassware.
2.3. Phthalate Metabolites Analysis
We used a previously described analytical method to determine phthalate monoester levels in urine samples [13]. We made some modifications to the previous method in the analytical column for serum phthalate metabolites analysis [48]. Briefly, we used high performance liquid chromatography electrospray ionization tandem mass spectrometry (HPLC-ESI-MS/MS), to analyze the level of urine samples for five phthalate metabolites: monobutyl phthalat (MBP), mono-benzyl phthalate (MBzP), mono-2-ethylhexyl phthalate (MEHP), mono-ethyl phthalate (MEP) and monomethyl phthalate (MMP). The limits of detection (LOD) of five phthalate metabolites were 1.4 ng/mL (MBP), 1.4 ng/mL (MBzP), 0.9 ng/mL (MEHP), 1.0 ng/mL (MEP) and 1.4 ng/mL (MMP).
2.4. Assay for Maternal Serum and Cord Serum Thyroid Hormones
Maternal serum and cord serum thyroid hormones, which include triiodothyronine (T3), thyroxin (T4), free T4 (FT4), and thyroid stimulating hormone (TSH), were analyzed using combined clinical chemistry and immunoassay tests (Modular Analytics Serum Work Area; Roche Diagnostics) and an electrochemoluminescence immunoassay (ECLIA) (Elecsys 2010 and Modular Analytics E170; Roche Diagnostics), respectively. Urinary creatinine level was re-analyzed and re-confirmed if the level exceeded the reference range.
2.5. Physical Examination of Health Status in Newborns
Physical examination and measurements of the newborns were done and recorded by the same pediatrician and a well-trained assistant. The measurements included the newborns’ birth anthropometric measurements, AGD and gestational age. To obtain an average AGD for each infant, AGD were measured twice. For female newborns, the AGD was measured from the center of the anus to the posterior convergence of the fourchette and to the junction of perineal skin with the rugated skin of the scrotum for male newborns [49].
2.6. Statistical Analysis
All statistical analysis was performed using SPSS 22.0 (IBM, Armonk, NY, USA). All the measured phthalate metabolites in maternal urine, serum and cord blood were log-transformed to approximate normal distribution. Covariate selection (e.g., age and gestational age, cigarette smoking, sex, birth weight, etc.) was based on the results of relevant studies [15,50]. We used Spearman and Pearson correlation coefficients to evaluate the correlation between each phthalate monoester in serum and thyroid hormone levels in fetus and parturient. We also used multiple linear regression to assess the associations among cord serum phthalate metabolites and cord serum thyroid hormone levels in newborns, adjusting for potential confounders in the forward stepwise regression model.
3. Results
3.1. Demographic Characteristics of Participants and Physical Examination of Newborns
The mean age of the participants was 34.0 ± 3.5 years (range: 26–43 years). The average gestation age at delivery was 39.0 ± 1.2 weeks. All our participants were non-smokers, but 11 participants had been exposed to passive smoke (18.3%). None of them were an “alcohol drinkers”, which was defined as “someone who consumed any alcohol at all during pregnancy”. No significant differences was observed between the levels of urinary phthalate metabolites and smoking habits and drinking. From the 76 initially recruited pregnant women, 61 foetuses were followed until birth. Significant differences between birth length, AGD and AGI-W were observed between male and female newborns; birth length (p < 0.01) and AGD (p < 0.01) were longer in males than females (Table 1).
3.2. Phthalate Metabolites in Maternal Urine, Serum, and Cord Blood
The detectable rates of MBP, MEHP, MEP, MMP and MBzP in all urine samples were 100%, 100%, 98%, 52% and 19%, respectively. Median levels without creatinine adjustments for five urinary phthalate metabolites at delivery were 114 ng/mL (25.4–1830) for MBP, 40.2 ng/mL (3.6–958) for MEHP, 36.4 ng/mL (ND-1980) for MEP, 8.3 ng/mL (ND-169) for MMP, and 5.7 ng/mL (ND-218) for MBzP (Table 2). Amongst the five urinary phthalate metabolites levels, MBP, MEP and MEHP were the highest, which suggests the predominant exposure to phthalates DBP, DEHP and DEP of our participants. The proportions of MBP, MEHP and MEP of total phthalate exposure were 59%, 18% and 16%, respectively.
The detectable rates of MBP and MEHP in all serum and cord serum samples were 100%, whereas MEP, MMP and MBzP were detected in less than 10% of all samples. Median levels of five phthalate metabolites in maternal serum at delivery were 158.0 ng/mL (59.6–1080) for MBP, 21.0 ng/mL (9.2–99.2) for MEHP, 2.8 ng/mL (ND-26.5) for MEP, ND ng/mL (ND-3.7) for MMP and ND ng/mL (ND-10.1) for MBzP (Table 2). Levels of MBP and MEHP in maternal serum were the highest of the five metabolites measured, which contributed over 95% of total phthalate exposure in pregnant women. The proportions of MBP and MEHP of total phthalate exposure in maternal serum were 87% and 11%, respectively.
In addition, the median levels of the five phthalate metabolites in cord serum were 256.0 ng/mL (65.2–815) for MBP, 24.7 ng/mL (11.0–665.0) for MEHP, ND ng/mL (ND-9.3) for MEP, ND ng/mL (ND-13.3) for MMP and ND ng/mL (ND-26.8) for MBzP (Table 2). Contribution profiles of MBP and MEHP in cord serum were quite similar to those in maternal serum. The proportions of MBP and MEHP of total phthalate exposure in cord serum were 90% and 9%, respectively.
3.3. Thyroid Hormone Levels in Pregnant Women and Newborns
We have compared the thyroid hormone levels of our participants to that of the general Taiwanese population, since there is no thyroid hormone reference range available for pregnant women and newborns. From our data, it is observed that more than 90% of T3, T4 and TSH levels in maternal serum samples were within the reference range of the general Taiwanese population. The low FT4 levels in our participants (more than 35% are lower than the lowest level of the general population) might suggest a possible mild thyroxine insufficiency (i.e., hypothyroidism). In addition, median levels of cord serum TSH and FT4 were higher than those in maternal serum (Table 3), whereas maternal serum T4 and T3 levels were much lower in the fetus. Although there is one outlier (hypothyroidism) which is excluded in the following analysis, the distribution of thyroid hormones in maternal serum and cord serum were not significantly changed.
3.4. Association between Phthalate Metabolites in Maternal Serum, Cord Serum and Thyroid Hormones
For maternal serum samples, significantly positive correlations were observed between levels of maternal serum T4 and FT4 (R = 0.76, p < 0.05), maternal serum T4 and T3 (R = 0.53, p < 0.05) and levels of maternal serum T3 and TSH (R = 0.39, p < 0.05) for pregnant women. For cord serum sample, significant positive correlation was also observed between levels of cord serum T4 and FT4 (R = 0.62, p < 0.05), and cord serum T4 and cord serum TSH (R = 0.35, p < 0.05) in newborns. However, no significant correlations were found between phthalate metabolites and thyroid hormones in maternal serum samples. In addition, a marginally significant negative trend between cord serum MBP and cord serum TSH (R = 0.25, p = 0.058), and cord serum MBP and cord serum T4 (R = 0.23, p = 0.092) was observed (Table 4). As cord serum MBP level increased, a decreasing trend of cord serum TSH in newborns was also observed (Figure 1).
3.5. Regression Analysis
A multiple regression model was used to examine the association between thyroid hormone level and phthalate metabolites in cord serum (Table 5). After adjusting for gestational age and maternal age (sex, cigarette smoking, birth weight and cord serum MEHP were excluded in the stepwise forward model), cord serum MBP levels showed a negative association with cord serum TSH (TSH: β = −0.217, p < 0.05), cord serum T4 (β = −1.71, p < 0.05) and cord blood TSH × T4 (β = −42.8, p < 0.05); however, we found a positive correlation between cord serum MBP and cord serum FT4/T4 (β = 0.036, p < 0.01).
4. Discussion
In this study, we found a correlation between higher exposure levels of cord serum phthalate and alterations in cord serum thyroid hormones in newborns. Despite having small sample size, the association between higher cord serum MBP level and low cord serum TSH and cord serum T4 remained after controlling for other variables in multiple regression model.The urinary phthalate metabolites levels in this study are consistent with our previous study [13], where we found that Taiwanese women (2005–2006) are exposed to a higher level of phthalates than the average American pregnant women [25], whereas their levels dropped dramatically after the 2011 DEHP scandal [15,42].
Some toxicological studies have shown possible thyroid hormone antagonist activities of certain phthalates, such as DBP and DEHP in adult animals [34,36,37,41]. Little information is available about phthalate exposure in the uterus and its effects on fetal thyroid. A two-generation study was conducted to evaluate the synergetic effect of PCB and DEP on adrenal and thyroid glands in rats. Follicular shrinkage, loss of thyroglobulin and fibrosis of the interfollicular epithelium was found in both treated parental and F1-generation male and female rats [38]. Another animal study has observed the morphological changes of the thyroid gland through the effect of DEHP [40].
Some possible mechanisms explaining how phthalates may alter thyroid hormones have been studied in experimental studies. Assessment of T3-antagonist activity using a thyroid hormone assay of three phthalates including BBzP and DBP done by a previous study showed TH-antagonist activities in vivo [37]. In addition, an investigation into the effects of six phthalates on transcriptional activity of sodium/iodide symporter (NIS) showed that DBP appeared to downregulate the human NIS promoter [43]. This suggested that phthalates such as DBP and DEHP could modulate transcriptional activity to induce thyroid hyperactivity and decrease the concentration of thyroxin. Besides, DEHP can perturb thyroid hormone homeostasis and reduce thyroid hormone levels through the activated Ras/Akt/TRHr pathway in thyroid-disrupting effects of DEHP [41].
Epidemiological studies [13,14,15,45,47,50] have shown possible effects on thyroid hormone homeostasis in humans. Some studies have reported that certain phthalate metabolites, such as MBzP, were inversely associated with cord serum TSH [16,17]. Phthalates indexes were also inversely associated with cord serum TSH and total T4 [17]. However Yao et al. did not observe any associations between urinary phthalate concentration and cord sera thyroid hormone [47]. Since phthalates can penetrate placenta [14,30,31,32] and clear clinical evidence of low maternal thyroid can affect thyroid function in newborns [51,52,53,54], it reveals that some phthalates, like DBP, may mimic functional thyroxin and cause a mildly decreased level of TSH in newborns. However, Minatoya et al. did not find any adverse effects of thyroid hormone levels in infants with prenatal DEHP exposure [46]. The discrepancies in results observed might be due to the possible differences in time of sample collection.
In this study, cord serum phthalate metabolites were observed to be higher than those in maternal serum. This might not indicate a possible placenta penetration of phthalate metabolites such as MBP and MEHP because we did not observe correlations between each pair of phthalate metabolites in maternal serum and cord serum. Hence, more research is needed to understand the possible underlying association and mechanism in the uterus. The knowledge of placenta transportation and metabolic ability of phthalates in uterus in animal studies [32] is much clearer than in humans. A previous study showed that DEHP and MEHP can penetrate the placenta [30] and some studies [55,56,57] have reported that phthalate metabolites existed in human serum as both a free and conjugated form. In addition, phthalates have also been detected in the urine of newborns [58]. Therefore, phthalates and phthalate metabolites may penetrate placenta by different mechanisms. These mechanisms may seem unclear, however it is possible that phthalate metabolites may penetrate placenta in its free form and accumulate in the fetus in its conjugated form. However, further studies are still needed to clarify this phenomenon.
Since more evidence showed the possible effects on thyroid hormone homeostasis for certain phthalates in animal and epidemiological studies [13,14,15,34,35,36,37,38,40,41,45,51], we cannot rule out the possible effect phthalate exposure has on thyroid function and other hormones [59,60,61]. Further research is still needed to clarify the possible mechanisms of such effect.
In addition to the limitations of this study previously described would be the small sample size and limited number of phthalate metabolites being analyzed [13], we did not measure the secondary metabolites of DEHP in this study. While we took precautions to prevent contamination during collection and analysis of serum samples, levels of phthalate metabolites in cord blood were higher than in maternal serum and distinguished profiles of phthalate metabolites in urine and serum samples were found (Figure 1). Urinary MBP, MEHP and MEP contributed over 95% of total phthalate exposure, whereas MBP and MEHP were dominantly compounds in serum and cord blood samples. Short-chain phthalates, like DEP and DMP, were rapidly metabolized to their metabolites in a few hours [62], which instantly excreted to urine and may not cause significant placenta transportation [63,64]. For long-chain phthalates with longer half-lives, like DBP and DEHP, continuous exposure to these phthalates through food and food packaging materials [18,65] are possible reasons that MBP and MEHP were both dominant compounds in serum and urine samples.
5. Conclusions
We found that the level of cord blood TSH in newborns was significantly negatively associated with MBP levels in cord blood after adjusting for covariates. The fall in TSH levels in newborns may be potentially delaying their development. Hence, questions about the relationship between thyroid and testosterone hormones in the uterus are needed for further investigation.
Author Contributions
Conceptualization, P.-C.H. and C.-C.L.; methodology, P.-C.H.; software, P.-C.H.; validation, P.-L.K. and W.-H.C.; formal analysis, P.-C.H. and W.-T.C.; investigation, P.-C.H., P.-L.K. and C.-C.L.; resources, P.-L.K. and C.-C.L.; writing—original draft preparation, P.-C.H.; writing—review and editing, S.-F.S., W.-H.C., P.-L.K., C.-C.L. and P.-C.H.; visualization, W.-T.C. and P.-C.H.; supervision, P.-L.K. and C.-C.L.; project administration, P.-C.H. and C.-C.L.; funding acquisition, P.-C.H. and C.-C.L. All authors have read and agreed to the published version of the manuscript.
Funding
This research was funded by Ministry of Science and Technology, Taiwan: NSC 93-2621-Z-006-005, Ministry of Science and Technology, Taiwan: NSC 94-2621-Z-006-005, Ministry of Science and Technology, Taiwan: NSC 95-2621-Z-006-005, National Health Research Institutes: EM-110-PP-11, Kaohsiung Medical University Research Center: KMU-TC109A01-1.
Institutional Review Board Statement
This study was approved by the Human Ethics Committee of the National Cheng Kung University Hospital with respect to scientific content.
Informed Consent Statement
Informed consent was obtained from all subjects involved in the study.
Data Availability Statement
The data are not publicly available due to protection of subjects’ privacy and confidentiality. The data presented in this study are available on request from the first author.
Acknowledgments
We thank all the participants who participated in this study. We thank the research nurse and assistants at the National Cheng Kung University Hospital for their assistance in specimen collection. This work was supported partially by the Research Center for Environmental Medicine, Kaohsiung Medical University, Kaohsiung, Taiwan from The Featured Areas Research Center Program within the framework of the Higher Education Sprout Project by the Ministry of Education (MOE) in Taiwan and by Kaohsiung Medical University Research Center Grant (KMU-TC109A01-1). We also thank the National Health Research Institutes for their partial financial support (Grant No.: EM-110-PP-11) and Ministry of Science and Technology (Grant No.: NSC 93-2621-Z-006-005, NSC 94-2621-Z-006-005 and NSC 95-2621-Z-006-005).
Conflicts of Interest
The authors declare they have no actual or potential financial interests or other potential conflicts of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results.
Abbreviations
| BBzP | butyl benzyl phthalate |
| BW | birth weight |
| BL | birth length |
| DBP | di-n-butyl phthalate |
| DEHP | di-(2-ethylhexyl) phthalate |
| DEP | di-ethyl phthalate |
| FT4 | free T4 |
| GA | gestational age |
| LC-ESI/MS/MS | liquid chromatography electrospray ionization tandem mass spectrometry |
| LOD | limit of detection |
| MBP | mono-n-butyl phthalate |
| MBzP | monobenzyl phthalate |
| MDL | minimum detectable limit |
| MEHP | mono-2-ethylhexyl phthalate |
| MEP | monoethyl phthalate |
| MMP | monomethyl phthalate |
| ND | not detectable |
| T3 | triiodothyronine |
| T4 | thyroxine |
| TSH | thyroid stimulation hormone |
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Figure and Tables
Enlarge this image.Figure 1. Relationship between log MBP levels and TSH levels in cord serum samples (n = 60).
Physical examination of health status in newborns (n = 61) a.
| Newborns’ Health Status | Males |
Females |
p-Value b |
|---|---|---|---|
| Birth weight (g) | 3250 | 3087 | |
| (1678–4260) | (2120–3935) | 0.055 | |
| Birth length (cm) | 50.4 | 48.7 | |
| (42.0–56.0) | (44.1–53.5) | <0.01 * | |
| Gestational age (weeks) | 39.1 | 38.7 | |
| (35.3–41.7) | (35.8–41.4) | 0.072 | |
| AGD (mm) a | 22 | 17 | |
| (12–36) | (7–23) | <0.01 * |
a The anogenital distances of one female and two male newborns were not available because of conducting blood infusion in the NICU. AGD = anogenital distance. b Wilcoxon rank sum test, * p < 0.05.
Table 2Concentrations of phthalate monoesters in urine, serum and cord blood in the third trimester before delivery (ng/mL, n = 61).
| Phthalate Monoesters | Urine | Serum | Cord Blood | |||
|---|---|---|---|---|---|---|
| Median (Range) | 10–90th | Median (Range) | 10–90th | Median (Range) | 10–90th | |
| MBP a | 114 (25.4–1830) | 36.9–550.6 | 158.0 (59.6–1080) | 64.9–413.0 | 256.0 (65.2–815) | 97.4–604.8 |
| MEHP | 40.2 (3.6–958) | 8.4–152.0 | 21.0 (9.2–99.2) | 11.7–37.1 | 24.7 (11.0–665.0) | 14.2–65.9 |
| MEP | 36.4 (ND b-1980) | 4.6–236.8 | 2.8 (ND-26.5) | ND-6.3 | ND (ND-9.3) | ND-3.4 |
| MBzP | 5.7 (ND-218.0) | 1.9–49.2 | ND (ND-10.1) | ND-2.8 | ND (ND-26.8) | ND-3.6 |
| MMP | 8.3 (ND-169) | 1.7–38.0 | ND (ND-3.7) | ND-2.4 | ND (ND-13.3) | ND-ND |
a MBP = monobutyl phthalate; MBzP = monobenzyl phthalate; MEP = monoethyl phthalate; MEHP = mono-2-ethylhexyl phthalate; MMP = monomethyl phthalate. b Detection limit (LOD) of phthalate monoesters were: MBP, 1.4; MBzP, 1.4; MEP, 1.0; MEHP, 0.9; MMP, 1.4 ng/mL, respectively. Half of LOD was calculated as the detected value below the LOD.
Table 3Concentrations of thyroid hormones in maternal serum and cord blood before delivery (n = 61).
| Heading | Maternal Serum 1 | Cord Blood | ||
|---|---|---|---|---|
| Median | Range | Median | Range | |
| TSH (μIU/mL) | 2.08 | 0.38–6.07 | 7.05 | 1.63–289.7 |
| T3 (ng/dL) | 140.0 | 82.4–277.4 | 56.3 | 35.1–84.6 |
| T4 (μg/dL) | 9.6 | 3.6–16.9 | 7.66 | 3.65–11.7 |
| FT4 (ng/dL) | 0.99 | 0.33–1.31 | 1.13 | 0.49–1.45 |
1 Reference values for thyroid hormones in Taiwan: TSH: 0.27–4.2; T3: 84.6–202.0; T4: 5.13–14.1; FT4: 0.93–1.7.
Table 4Spearman correlation coefficients between thyroid hormones and phthalate monoesters in serum samples (n = 60) a.
| Maternal Serum | Cord Serum | |||||||
|---|---|---|---|---|---|---|---|---|
| T4 | T3 | FT4 | TSH c | T4 | T3 | FT4 | TSH c | |
| T4 | - | - | ||||||
| T3 | 0.53 * | - | 0.15 | - | ||||
| FT4 | 0.76 * | 0.20 | - | 0.62 * | 0.25 | - | ||
| TSH | 0.13 | 0.39 * | 0.16 | - | 0.35 * | 0.03 | 0.21 | - |
| MBP | −0.08 | −0.11 | −0.14 | −0.06 | −0.23 + | 0.11 | 0.10 | −0.25 # |
| MEHP | 0.01 | 0.19 | −0.11 | 0.08 | −0.04 | 0.18 | 0.01 | −0.07 |
| MEP | −0.14 | −0.17 | −0.06 | −0.13 | −0.05 | 0.09 | −0.07 | 0.05 |
| Age b | −0.10 | −0.15 | 0.05 | 0.04 | −0.09 | −0.03 | 0.10 | −0.04 |
a *: p < 0.05; #: p < 0.06; +: p < 0.10. b Current age for pregnant women and gestational age for newborns. c TSH in cord serum and maternal serum were log-transferred.
Table 5Multiple linear regression between TSH and T4 levels and their corresponding phthalate metabolites in cord serum (n = 60) a.
| Variables | TSH (μIU/mL) | TSH × T4 | TSH × FT4 | FT4/T4 | T4 (μg/dL) | |||||
|---|---|---|---|---|---|---|---|---|---|---|
| Estimate | p | Estimate | p | Estimate | p | Estimate | p | Estimate | p | |
| Intercept | 3.49 | 0.010 | 171.4 | 0.004 | 20.6 | 0.001 | 0.123 | 0.006 | 20.4 | 0.017 |
| MBPcord serum | −0.217 | 0.044 * | −42.8 | 0.028 * | −4.49 | 0.075 # | 0.036 | 0.004 ** | −1.71 | 0.036 * |
| Maternal age | — | — | — | — | — | — | −0.002 | 0.087 # | 0.113 | 0.106 |
| Gestational age | −0.045 | 0.117 | — | — | — | — | — | — | −0.315 | −0.104 |
| R2 | 0.087 | 0.044 | 0.092 | 0.028 | 0.054 | 0.075 | 0.171 | 0.005 | 0.115 | 0.046 |
a All the parameters were log-transformed. Estimate values are beta coefficients except for R2; # p < 0.10. * p < 0.05. ** p < 0.01. —, Excluded from stepwise forward model.
© 2021 by the authors.
Details
; Wei-Hsiang, Chang 3 ; Shu-Fang, Shih 4 ; Wan-Ting, Chang 5 ; Ching-Chang, Lee 6 1 National Institute of Environmental Health Sciences, National Health Research Institutes, Miaoli 350, Taiwan;
2 Department of Obstetrics and Gynecology, Medical College, National Cheng Kung University, Tainan 701, Taiwan;
3 Department of Food Safety/Hygiene and Risk Management, National Cheng Kung University, Tainan 701, Taiwan;
4 Department of Health Administration, College of Health Professions, Virginia Commonwealth University, Richmond, VA 23284, USA;
5 National Institute of Environmental Health Sciences, National Health Research Institutes, Miaoli 350, Taiwan;
6 Research Center of Environmental Trace Toxic Substances, College of Medicine, National Cheng Kung University, Tainan 701, Taiwan; Department of Environmental and Occupational Health, Medical College, National Cheng Kung University, Tainan 701, Taiwan