Skip to content

Environmental Health Perspectives

Facebook Page EHP Twitter Feed Open Access icon  

Research December 2017 | Volume 125 | Issue 12

Environ Health Perspect; DOI:10.1289/EHP2019

Uterine Artery Flow and Offspring Growth in Long-Evans Rats following Maternal Exposure to Ozone during Implantation

Colette N. Miller,1 Janice A. Dye,1 Allen D. Ledbetter,1 Mette C. Schladweiler,1 Judy H. Richards,1 Samantha J. Snow,1 Charles E. Wood,2 Andres R. Henriquez,3 Leslie C. Thompson,1 Aimen K. Farraj,1 Mehdi S. Hazari,1 and Urmila P. Kodavanti1
Author Affiliations open

1Environmental Public Health Division, National Health & Environmental Effects Research Laboratory, Office of Research and Development, U.S. Environmental Protection Agency (EPA), Research Triangle Park, North Carolina, USA

2Integrated Systems Toxicology Division, National Health & Environmental Effects Research Laboratory, Office of Research and Development, U.S. EPA, Research Triangle Park, North Carolina, USA

3Curriculum in Toxicology, University of North Carolina School of Medicine, University of North Carolina-Chapel Hill, Chapel Hill, North Carolina, USA

PDF icon PDF Version (1.5 MB)

  • Background:
    Epidemiological studies suggest that increased ozone exposure during gestation may compromise fetal growth. In particular, the implantation stage of pregnancy is considered a key window of susceptibility for this outcome.
    Objectives:
    The main goals of this study were to investigate the effects of short-term ozone inhalation during implantation on fetal growth outcomes and to explore the potential for alterations in uterine arterial flow as a contributing mechanism.
    Methods:
    Pregnant Long-Evans rats were exposed to filtered air, 0.4ppm ozone, or 0.8ppm ozone for 4 h/d during implantation, on gestation days (GD) 5 and 6. Tail cuff blood pressure and uterine artery Doppler ultrasound were measured on GD 15, 19, and 21. To assess whether peri-implantation ozone exposure resulted in sustained pulmonary or systemic health effects, bronchoalveolar lavage fluid, serum metabolic and inflammatory end points, and kidney histopathology were evaluated in dams at GD 21. Growth parameters assessed in GD 21 offspring included fetal weight, length, and body composition.
    Results:
    Measures of maternal uterine arterial flow, including resistance index and mean velocity, indicated that resistance increased between GD 15 and GD 21 in 0.8ppm dams but decreased in controls, although absolute values were similar in both groups on GD 21. Ozone-exposed dams also had lower serum glucose and higher free fatty acid concentrations than controls on GD 21. On GD 21, both male and female offspring had lower body weight than controls, and pooled subsets of 3 male and 3 female fetuses from litters exposed to 0.8ppm ozone had lower lean mass and fat mass than pooled control offspring.
    Conclusions:
    Findings from our experimental model suggest that the offspring of dams exposed to ozone during implantation had reduced growth compared with controls, possibly as a consequence of ozone-induced vascular dysfunction. https://doi.org/10.1289/EHP2019
  • Received: 10 April 2017
    Revised: 7 November 2017
    Accepted: 13 November 2017
    Published: 21 December 2017

    Address correspondence to C.N. Miller, U.S. Environmental Protection Agency, NHEERL/EPHD/CIB, 109 T.W. Alexander Dr., Mail Code: B105-02, Research Triangle Park, NC 27711. Telephone: 919-541-3469. Email: miller.colette@epa.gov

    Supplemental Material is available online (https://doi.org/10.1289/EHP2019).

    The authors declare they have no actual or potential competing financial interests.

    Note to readers with disabilities: EHP strives to ensure that all journal content is accessible to all readers. However, some figures and Supplemental Material published in EHP articles may not conform to 508 standards due to the complexity of the information being presented. If you need assistance accessing journal content, please contact ehponline@niehs.nih.gov. Our staff will work with you to assess and meet your accessibility needs within 3 working days.

  • PDF icon Supplemental Material PDF (262 KB)


    Note to readers with disabilities: EHP has provided a 508-conformant table of contents summarizing the Supplemental Material for this article (see below) so readers with disabilities may determine whether they wish to access the full, nonconformant Supplemental Material. If you need assistance accessing journal content, please contact ehponline@niehs.nih.gov. Our staff will work with you to assess and meet your accessibility needs within 3 working days.
    PDF icon Supplemental Table of Contents PDF (144 KB)

Introduction

Intrauterine growth restriction (IUGR) is an adverse pregnancy outcome defined by Peleg et al. (1998) as a reduction in fetal weight (below the 10th percentile for gestational age) with an abdominal circumference below the 2.5th percentile, although inconsistencies in the definition of IUGR exist. IUGR affects 5.8–11.2% of all pregnancies in the United States, varying by ethnicity (Kramer 2003), and 23.8% of pregnancies in developing countries (de Onis et al. 1998). Growth-compromised offspring have increased risk of perinatal death (Bernstein et al. 2000) and of later-in-life adverse health outcomes including neurodevelopmental delay (Murray et al. 2015) and cardiometabolic diseases (Cianfarani et al. 2012). The pathogenesis of IUGR is complex and incompletely understood (Sankaran and Kyle 2009), and effective prevention recommendations and treatment options are currently limited.

Known risk factors for IUGR include, but are not limited to, poor maternal nutrition, infection, gestational hypertension (preeclampsia), and diabetes (Albu et al. 2014). With regard to air pollutants, studies have found relationships between prenatal ozone exposure and reduced birth weight (Zheng et al. 2016). More specifically, Tu et al. (2016) reported that ambient ozone was inversely associated with term birth weight among 105,818 singleton births in the state of Georgia. Similarly, a study in 3,545,177 singleton births in California also demonstrated an inverse relationship with ozone exposure and birth weight (Morello-Frosch et al. 2010). In contrast, others have not found associations between ozone exposure during pregnancy and fetal weight. For example, Liu et al. (2007) failed to find a positive association between IUGR and gestational ozone exposure in Canadian singleton births between 1986 and 2000; Gouveia et al. (2004) also did not find a relationship between ozone exposure and low birth weight in 213,973 births in São Paulo, Brazil. Inconsistent findings among observational studies may be related to differences in seasonal temperature or to variability in sensitivity at different stages of gestation. Arroyo et al. (2016) reported a positive relationship between second-trimester ambient temperature and low birth weight, as well as a similar relationship between first-trimester ozone exposure and birth weight in all singleton births in Madrid, Spain between 2001 and 2009. Additionally, Geer et al. (2012) reported that estimated ozone exposure during the first and second trimesters was associated with lower term birth weight among >1,500,000 births in Texas between 1998 and 2004. Further, among California participants in the Children’s Health Study, positive associations between ozone and IUGR were reported for exposures during both the second and third trimesters (Salam et al. 2005). Thus, the influence of the period during gestation in which exposure to ozone takes place requires further study.

Adverse pregnancy outcomes such as IUGR may initiate from suboptimal implantation in the uterine wall [reviewed by Young et al. (2010)]. It is hypothesized that disrupted stem cell invasion may lead to poor spiral and uterine artery remodeling with subsequent impaired placental development. In turn, the stress from diminished uterine arterial blood flow and insufficient placental nutrition may result in maternal systemic endothelial dysfunction and inflammation, hypertension, and kidney injury related to glomerular damage. Poor arterial remodeling also impairs fetal blood flow, which may promote disrupted placental development and decreased fetal weight gain.

Given this evidence, we hypothesized that ozone exposure exclusively during the period of implantation receptivity in the rat would compromise fetal growth and maternal health in late gestation. Anticipating that impairments in fetal growth may be related to diminished uterine arterial flow, we used Doppler ultrasonography periodically throughout gestation to assess changes in uterine artery blood flow. The duration of implantation receptivity in rats and humans is similar (2 d). Thus, investigating the effects of ozone exposure during the time of implantation may provide a plausible mechanism that links gestational ozone exposure and IUGR.

Methods

Rats and Experimental Design

Timed-pregnant Long-Evans female rats (n=10/group) from Charles River Laboratories were transferred to the U.S. Environmental Protection Agency (EPA) animal facility on gestation day (GD) 1 (plug-positive day). All procedures involving animals were approved by the Institutional Animal Care and Use Committee at the National Health and Environmental Effects Research Laboratory, an Association for Assessment and Accreditation of Laboratory Animal Care (AAALAC)-accredited facility. All animals were treated humanely and with regard for alleviation of suffering. A modified, phytoestrogen-free American Institute of Nutrition growth and lactation diet (D15092401; Research Diets) was provided ad libitum to dams after arrival. Food intake and body weight were measured daily. The primary caretaker was blinded to the exposure groups throughout the study.

Rats were randomly assigned to one of three groups: filtered air, 0.4ppm ozone, or 0.8ppm ozone. These concentrations were selected based on evidence that there is a four- to five-fold difference in relative lung ozone dosimetry between resting rats and humans exercising heavily on an intermittent basis, as determined by heavy (18O-labeled) reaction product concentrations in the lung (Hatch et al. 1994). Thus, the 0.4 and 0.8ppm concentrations in rats correspond approximately to 0.08 and 0.16ppm exposure concentrations, respectively, in humans. The approved 2015 U.S. national ambient air quality standard (NAAQS) for ozone is 0.070ppm, with an 8-h averaging time (U.S. EPA 2015).

On GD 5 and 6, rats were exposed for 4 h (0700–1100 hours) in Rochester-style “Hinners” chambers that were controlled for temperature (22.5±0.14°C) and humidity (50.0±0.65%). Ozone was generated in a silent arc discharge generator (OREC™) and was pumped into the chambers using a mass flow controller. Concentrations were recorded throughout the exposure using an ozone analyzer (API Model 400; Teledyne Instruments). To quantify the extent of ozone-induced ventilatory dysfunction (which has not been previously reported in pregnant Long-Evans rats), conscious, unrestrained rats were placed in whole-body plethysmographs immediately following exposure. Estimates of tidal volume, breathing frequency, minute volume, peak flow rates, and enhanced pause [Penh; an index of airflow limitation and a surrogate measure for bronchoconstriction (Hamelmann et al. 1997)] were obtained using emka iox2 software (emka TECHNOLOGIES).

On GD 15, 19, and 21, blood pressure was measured using tail cuff photoplethysmography. Rats were acclimated to a plexiglass restraint tube for 5 min at 22.2–23.3°C and then for 5 min in a prewarmed 32°C chamber. Tail blood pressure was determined from 3–5 readings of each rat on an IITC Life Science Inc. system and was analyzed using Model 31 NIBP software (v.1.32; IITC Life Science Inc.).

Uterine Artery Blood Flow

Because blood flow through the uterine artery does not increase until GD 14 (Osol and Mandala 2009), we assessed uterine arterial blood flow after that time point. On GD 15, 19, and 21, pulsed-wave Doppler ultrasonography (Vevo 2100 Imaging System; FUJIFILM VisualSonics Inc.) was performed to evaluate blood flow in the left uterine artery, similar to procedures that have been described previously (Qu et al. 2014). In brief, rats were anesthetized with 3% isoflurane and were maintained at 1.5% with a targeted heart rate range of 400–450 beats per minute. Dams were placed in dorsal recumbency on a heated monitoring platform (FUJIFILM VisualSonics Inc.), which allowed monitoring of heart rate and electrocardiogram (ECG) traces, respiration rate, and body temperature. Fur was clipped from the abdomen, and a depilatory agent was used to remove any remaining fur. Pulsed-wave Doppler ultrasonography was performed using a 12.5-MHz MS201 transducer (FUJIFILM VisualSonics Inc.). All measurements and analyses were performed using Vevo LAB software (v.1.7, FUJIFILM VisualSonics Inc.) by researchers who were blinded to the experimental groups. Data were derived by analyzing six arterial pulsatile blood flow waveforms from each dam at each time point. Peak systolic velocity (PSV) was measured at the point of peak velocity, and end diastolic velocity (EDV) was marked at the next ECG R-wave after PSV was measured (Figure 1). Markers of resistance were calculated using the following formulas: resistanceindex=(PSVEDV)/PSV; pulsatilityindex=(PSVEDV)/meanbloodvelocity(mV); and systole/diastole(S/D)ratio=(PSV/EDV).

Doppler ultrasonography waveform showing the equations RI equals open parenthesis PSV minus EDV close parenthesis divided by PSV; S virgule D ratio equals PSV divided by EDV; and PI equals open parenthesis PSV minus EDV close parenthesis divided by mean velocity. Velocity is measured in millimeters per second.

Figure 1. Equations of the resistance indices in Doppler ultrasonography. Resistance in the artery can be measured through resistance index (RI) [peak systolic velocity (PSV) – end diastolic velocity (EDV)/(PSV)], systolic/diastolic (S/D) ratio (PSV/EDV), and the pulsatility index (PI) [(PSV – EDV)/mean blood velocity (mV)].

Necropsy and Tissue Collection

On GD 21, dams were euthanized with a lethal intraperitoneal dose of pentobarbital (>400 mg/kg) following a 5 h fast; this dose also euthanized the fetuses in utero. Whole blood was obtained from the abdominal aorta and was collected into serum separator tubes and ethylenediamine tetraacetic acid (EDTA) tubes for plasma collection. Following centrifugation for 10 min at 2,465 × g and 4°C, aliquots were prepared from the resulting supernatant and were stored at 80ºC until use. Bronchoalveolar lavage fluid (BALF) was collected and analyzed from dams as previously described (Wallenborn et al. 2009). Briefly, the following markers of pulmonary injury were assessed: total protein (μg/mL BALF), albumin (μg/mL BALF), lactate dehydrogenase (LDH) activity [U/L (units per liter) BALF], N-acetyl glucosaminidase (NAG) activity (U/L BALF), and γglutamyl transferase (GGT) activity (U/L BALF). The following markers of pulmonary inflammation were assessed: alveolar macrophages, eosinophils, lymphocytes, and neutrophils. The right kidney was collected, divided midsagittally, placed in Bodian’s fixative (2% formaldehyde, 5% acetic acid, 72% ethanol, and 21% water), and stored at 4°C for histopathology. The gravid uterus was weighed and assessed for implantation sites. Fetuses were counted and assessed for crown-rump length, weight, and sex. Ultimately, one dam from the air group and one dam from the 0.4ppm ozone–exposed group were removed from the study at the time of necropsy owing to insufficient litter size (n<5fetuses). Excessively small litters reduce maternal nutritional requirements (Mattingly and Mcclure 1982) and promote larger fetal size because of reduced competition for nutrients within the litter (Romero et al. 1992).

Circulating Metabolic Markers

Serum norepinephrine was measured using a Norepinehprine Research ELISA kit (Rocky Mountain Diagnostics, Inc.), and corticosterone was measured using an enzyme immunoassay kit (Arbor Assays) according to the manufacturers’ protocols. Serum glucose was measured using a Glucose (oxidase) Reagent set, total cholesterol was measured using an Enzymatic Liquid kit, and triglycerides were measured using a GPO Trinder kit (all from TECO Diagnostics). High-density lipoprotein (HDL) and low-density lipoprotein (LDL) cholesterol were measured using automated reagents (Sekisui Diagnostics). Serum free fatty acids (FFAs) were measured using a colorimetric assay (Cell Biolabs, Inc.). The cholesterol and FFA assays were modified for use on a Konelab Arena 30 system (Thermo LabSystems Inc.). Plasma insulin was detected using a Rat/Mouse Insulin ELISA (Millipore), and branched chain amino acid plasma levels were detected using a Branched Chain Amino Acid Assay kit (Abcam).

Inflammatory Measurements

Preeclampsia is associated with increased serum inflammatory status in the mother (Mihu et al. 2015). Hence, inflammation markers were measured in maternal serum using a Meso Scale Proinflammatory Panel 2 kit for rats on a Meso Scale QuickPlex SQ 120 system (Meso Scale Diagnostics, LLC). This predesigned kit provided a broad spectrum of proinflammatory cytokines in a multiplexed assay including interferonγ (IFNγ), interleukin1β (IL1β), interleukin 4 (IL4), interleukin 5 (IL5), interleukin 6 (IL6), interleukin 10 (IL10), interleukin 13 (IL13), keratinocyte chemoattractant/human growth-regulated oncogene (KC-GRO), and tumor necrosis factorα (TNFα). Assay was performed according to the manufacturer’s protocols.

Histopathology

After fixation, right kidneys were embedded in paraffin wax and sectioned at 5 μm. Kidney sections were deparaffinized and stained with hematoxylin and eosin (H&E) (BBC Biochemical) using standard procedures and were evaluated via light microscopy by a certified study pathologist (C.E.W.). According to best practices for nonclinical safety studies (Crissman et al. 2004), primary histopathological review was performed unblinded to experimental treatment, and findings that might have been treatment-related or might otherwise have affected interpretation were re-reviewed in a blinded manner to confirm differences from controls, severity grade, or both. Histopathological diagnoses were based on standard criteria and nomenclature (Frazier et al. 2012). Severity of lesions was qualitatively graded using a 0–4 scale (0=absent, 1=minimal, 2=mild, 3=moderate, 4=severe) based on increasing extent, complexity of change, or a combination of the two.

Fetal Body Composition Measurements

At necropsy, three arbitrarily selected fetuses from each sex were grouped from each dam and were stored at 4°C. If there was an insufficient number of fetuses, a measurement could not be obtained. Hence, an n=7/litter group was analyzed for air and for 0.8ppm ozone, whereas an n=8/litter group was analyzed for 0.4ppm ozone. After warming to room temperature (22.2–23.3°C), body composition (grams of fat and lean body mass) was measured using magnetic resonance on the n=3 representative grouping for each litter (measured at the same time) using an EchoMRI™-100 system (EchoMRI™) at the University of North Carolina at Chapel Hill Nutrition Obesity Research Center.

Statistics

For fetal growth metrics, all analyses were performed separately by sex, and litters were pooled by sex. Data were analyzed using a two-tailed Fisher’s least significant difference (LSD) test for all planned multiple comparisons (filtered air vs. 0.4ppm vs. 0.8ppm ozone for all data) within a one-way analysis of variance (ANOVA) (GraphPad Prism v.6; GraphPad Software, Inc.). Fisher’s LSD test does not correct for multiple comparisons; however, it can be used in study designs with three groups without increasing Type I error rate (Liu and Tu 2008). Upon determining that fetal weight was reduced in fetuses from ozone-exposed pregnancies, a priori body composition measurements were performed. Therefore, a one-tailed Fisher’s LSD test within a one-way ANOVA was used to assess differences in fetal body composition. Finally, because renal pathology findings were only assessed in the positive direction (i.e., increasing pathological changes), histopathology incidence data were analyzed using a one-sided Fisher’s exact test. For all measurements, significance was set at p<0.05.

Results

Effects of Ozone Exposure during Implantation on Dams

Food intake and body weight were monitored throughout gestation as markers of growth and overall maternal health. Because the size of the litter affects the nutrient demands of the pregnant rodent (Mattingly and Mcclure 1982), the two dams having litters with <5 fetuses (one from the air group and one from the 0.4ppm ozone group) were removed from all analyses in the study. Exposure to 0.8ppm ozone reduced 48 h body weight gain and food intake in pregnant dams over the exposure period (difference between GD 5 and GD 7) (Figure 2A, B). There were no significant differences between treatment groups in total weight gain or in food intake during pregnancy (Table 1).

Figure 2A is a line graph plotting maternal body weight in grams (y-axis) across days ranging from 0 to 21 with an interval of 7 days (x-axis) for exposure to air and exposure to 0.4 parts per million and 0.8 parts per million ozone. Inset is a bar graph with standard errors plotting 48 hour mean weight gain (y-axis) across the aforementioned three treatment groups (x-axis). Figure 2B is a scatter plot that presentes maternal food intake in grams (y-axis) across days ranging from 0 to 21 with an interval of 7 days (x-axis) for the aforementioned three treatment groups. Standard errors are also indicated. Figure 2C is a bar graph with standard errors plotting mean Penh (y-axis) across GD 5 (exposed to ozone), 6 (exposed to ozone), 15, 19, and 21 (x-axis) for the aforementioned three treatment groups. Figure 2D is a bar graph with standard errors plotting minute volume in milliliters per minute (y-axis) across GD 5 (exposed to ozone), 6 (exposed to ozone), 15, 19, and 21 (x-axis) for the aforementioned three treatment groups.

Figure 2. Average maternal body weight, food intake, and respiratory parameters following ozone exposure (0.4ppm, n=9, or 0.8ppm, n=10) or air exposure (n=9). (A) Mean body weight (g) according to treatment group and gestational day (GD), with the insert showing the mean weight gain over 48 h (from GD 5 to GD 7). (B) Mean food intake (g) according to treatment group and GD. (C) Mean enhanced pause (Penh) according to treatment group on GD 5, 6, 15, 19, and 21. (D) Mean minute volume (mL/min) according to treatment group (GD 5, 6, 15, 19, and 21). Error bars indicate the standard error. Data were analyzed by two-tailed Fisher’s least significant difference (LSD) posttest within a one-way analysis of variance (ANOVA). * p<0.05, *** p<0.001, **** p<0.0001 versus air controls; # p<0.05, 0.4ppm versus 0.8ppm ozone.

Table 1. Litter characteristics according to exposure group [mean±standarderrorofthemean(SE)].
Characteristics Aira 0.4ppma 0.8ppm ANOVA p-valueb (totals)
Total number of litters maintained to GD 21 9 9 10
Gestational weight gain (g) 152.4±5.83 147.6±5.91 139.6±6.81 0.35
Gestational food intake (g) 521.6±15.8 492.9±18.4 503.2±16.8 0.50
Implantation sites per litter 13.5±0.64 14.1±0.59 13.2±0.57 0.57
Resorptions per litter 1.4±0.31 2.1±0.77 1.5±0.50 0.62
Full term fetuses 12.1±0.50 12.0±0.37 11.7±0.72 0.87
Percent males per litter 47.0±3.95% 50.6±4.55% 50.4±5.24% 0.85

Note: ANOVA, analysis of variance; GD, gestational day.

aOwing to low litter size (<5 fetuses), one rat each was removed from the air and the 0.4ppm group data sets.

bData were analyzed by two-tailed Fisher’s least significant difference (LSD) posttest within a one-way ANOVA.

Whole-body plethysmography assessments performed immediately after ozone exposure on GD 5 and 6 and assessments of controls were performed at the same time of day. Penh, an index of airway resistance, was significantly higher in the 0.8ppm ozone group than in controls on both days and in the 0.4ppm ozone group on GD 5 (Figure 2C), whereas minute volume was significantly lower in the 0.8ppm ozone group compared with controls on GD 6 (Figure 2D). However, both Penh and minute volumes were comparable among controls and both exposure groups on GD 15, 19, and 21. Therefore, exposure to ozone did not appear to have lasting effects on respiratory parameters after GD 15.

Ultrasonography of Uterine Arterial Blood Flow

We used Doppler ultrasonography to assess the effects of ozone exposure during implantation on maternal uterine artery blood flow at various points during gestation. In a normal pregnancy, resistance to blood flow decreases in the uterine artery, which facilitates perfusion of the fetoplacental unit (Mose 2014). In air-exposed dams, mean uterine arterial resistance [represented by the resistance index (RI)] decreased 3.3% (±2.8%) from GD 15 and 21, and mV increased 4.6% (±8.6%) (Figure 3B, E; see also Table S1). The mean RI for 0.8ppm ozone–exposed dams was slightly lower than that of controls on GD 15 (0.59±0.01 vs. 0.61±0.01, respectively) but was comparable to that of controls on GD 21 (both 0.60), resulting in a 2.2% increase (±2.1%, p<0.10) from GD 15 and GD 21, in contrast to a 3.3% decrease (±2.8%) in the controls over the same time period. Patterns were similar for the systolic/diastolic (S/D) ratio and the pulsatility index (PI) (Figure 3C, D; see also Table S1), which are additional indicators of resistance. The average mV was significantly higher in 0.8ppm ozone–exposed dams than in controls on GD 15, and although it decreased from GD 15 to GD 21 (23%±9.2%), there was no significant difference in the average mV between 0.8ppm dams and controls on GD 21 (Figure 3E; see also Table S1).

Figure 3A is a Doppler ultrasound for air control and exposure to 0.8 parts per million ozone on GD 21. Figures 3B, 3C, 3D, and 3E are box and whisker plots respectively plotting resistance index (percent change GD 15 to GD 21), S/D ratio (percent change GD 15 to GD 21), pulsatility index (percent change GD 15 to GD 21), and mean blood velocity (percent change GD 15 to GD 21) (y-axis) across the following treatment groups: exposure to air and exposure to 0.4 parts per million and 0.8 parts per million ozone.

Figure 3. Percent difference in uterine artery flow metrics measured on gestational day (GD) 15 to GD 21 in dams exposed to air (n=9), to 0.4ppm ozone (n=9), or to 0.8ppm ozone (n=10) on GD 5 and GD 6. (A) An example of a representative Doppler ultrasound waveform for uterine artery flow on GD 21 and shows that measures of resistance [resistance index (RI), systolic/diastolic (S/D) ratio, and pulsatility index (PI)] from Doppler ultrasound are performed by quantifying the relative distance between systole (S) and diastole (D); increased distance between S and D indicates increased resistance. (BE) The percentage difference between GD 15 and GD 21 in the RI, S/D ratio, PI, and mean blood velocity (mV), respectively (see Table S1 for corresponding numeric data). Data analyzed by two-tailed Fisher’s least significant difference (LSD) posttest within a one-way analysis of variance (ANOVA). Boxes extend from the 25th to the 75th percentile, horizontal bars represent the median, whiskers indicate the 10th and 90th percentiles, and outliers are represented as points. Values for individual dams are overlaid on each plot. # p<0.10 and * p<0.05 versus air controls.

Effects of Peri-implantation Ozone Exposure on Maternal Health in Late Gestation

Early gestational ozone exposure did not significantly alter blood pressure, as measured using a tail cuff, in later pregnancy (GD 15, 19, and 21; see Figure S1). No significant group differences in kidney histopathology were observable by light microscopy (see Table S2).

Examination of a panel of nine proinflammatory cytokines in the serum of dams on GD 21 revealed no significant differences among the control and treatment groups (see Table S3). In addition, there were no significant differences among groups in BALF cell counts (alveolar macrophages or other leukocytes) or in protein concentrations in BALF collected on GD 21 (see Table S4). BALF concentrations of GGT and NAG were significantly higher in 0.4ppm ozone–exposed dams than in controls, but concentrations in BALF from 0.8ppm dams were not significantly different from those in controls.

Effects of Peri-implantation Exposure to Ozone on Developmental End Points

All dams successfully maintained their pregnancies to GD 21. After excluding one dam from the control group and one from the 0.4ppm ozone group that each had <5 fetuses per litter, there were no significant differences among the treatment groups with regard to implantation sites or resorptions on GD 21, or with regard to the sex distribution of the fetuses (Table 1).

There were no significant differences among treatment groups in the average length of male and female fetuses from each litter on GD 21 (Figure 4A and B, respectively). However, average weights of fetuses in each litter were lower in the litters exposed to 0.4ppm and 0.8ppm ozone on GD 5 and 6 compared with controls (significant for males in both exposed groups and for females in the 0.8ppm group). Reduced fetal weight with normal fetal length is consistent with asymmetrical IUGR, which is purportedly related to reduced fetal nutrition and oxygen supply in the second half of pregnancy (Moh et al. 2012); this is in contrast with symmetrical IUGR, in which both weight and length are reduced owing to poor cellular development in the first trimester, the second trimester, or in both (Brodsky and Christou 2004).

Figures 4A and 4B are box and whisker plots, plotting litter average values in males and females, respectively (y-axis), across length in centimeters and weight in grams (x-axis) for the following treatment groups: exposure to air and exposure to 0.4 parts per million and 0.8 parts per million ozone. Figures 4C and 4D are box and whisker plots, plotting litter average values in males and females set to air control, respectively (y-axis), across fat mass and lean mass (x-axis) for the aforementioned treatment groups. Figures 4E and 4F are box and whisker plots, plotting litter average values for fat mass to lean mass ratio in males and females, respectively (y-axis), across the aforementioned treatment groups (x-axis).

Figure 4. Body size measurements in male and female offspring on gestational day (GD) 21 according to treatment group and sex. (A) and (B) Distribution of litter average values for length (cm) and weight (g) in males and females, respectively, from each litter (n=9, 9, and 10litters for air, 0.4ppm ozone, and 0.8ppm ozone groups, respectively). (C) and (D) Distribution of litter average values for fat mass and lean mass (relative to controls) in males and females, respectively (n=3 fetuses pooled per litter for each group and sex; n=7, 8, and 7 litters for air, 0.4ppm ozone, and 0.8ppm ozone groups, respectively). (E) and (F) Distribution of litter average values for fat mass to lean mass ratio in males and females, respectively (calculated by the obtained fat and lean mass for the n=3 fetuses pooled per litter for each group and sex; n=7, 8, and 7 litters for air, 0.4ppm ozone, and 0.8ppm ozone groups, respectively). The data were analyzed by one-way analysis of variance (ANOVA) within a two-tailed Fisher’s least significant difference (LSD) posttest (for length and weight) or a one-tailed Fisher’s LSD posttest (for fat mass, lean mass, and fat-to-lean mass ratios). Boxes extend from the 25th to the 75th percentile, horizontal bars represent the median, whiskers indicate the 10th and 90th percentiles, and outliers are represented as points. Average values for individual litters (by sex) are overlaid on each plot. # p<0.10, * p<0.05, ** p<0.01 versus air controls.

Because asymmetrical IUGR is associated with reduced adipose tissue deposition due to decreased nutritional supply in the second half of pregnancy (Lapillonne et al. 1997), we next investigated the potential influence of ozone-induced growth restriction on the body composition of the offspring. Average litter values for lean mass and fat mass (based on pooled data for 3 randomly selected male and female fetuses from each litter) were lower in the ozone-exposed litters (n=8 for 0.4ppm, n=7 for 0.8ppm) than in controls (n=7), with significant differences from controls (based on the one-tailed Fisher’s LSD posttest) in the 0.8ppm groups for both outcomes in both male and female fetuses (Figure 4C, D). The ratio of fat mass–to–lean body mass [fat mass (g)/lean body mass (g) of the pooled group for each litter, separated by sex] was then assessed because asymmetrical IUGR is related to reduced fat development in utero (Lapillonne et al. 1997), and the ratio provides an estimate of relative adiposity. Although the fat-to-lean mass ratio was not statistically different (based on the one-tailed Fisher’s LSD posttest) in female offspring from ozone-exposed pregnancies, male offspring from 0.8ppm ozone–exposed dams had a modest, nonstatistically significant reduction in fat mass relative to lean mass (p=0.06; Figure 4E, F).

Mean serum FFAs on GD 21 were significantly higher in dams exposed to either concentration of ozone than in air controls (Figure 5A), whereas mean blood glucose concentrations were significantly lower in ozone-exposed dams (Figure 5B). There were no significant differences in other maternal serum parameters on GD 21, including insulin and triglycerides, among the treatment groups (see Table S5).

Figures 5A and 5B are box and whisker plots respectively plotting free fatty acids (y-axis) and glucose (y-axis) both in milligrams per deciliter for the following treatment groups (x-axis): exposure to air and exposure to 0.4 parts per million and 0.8 parts per million ozone.

Figure 5. Serum free fatty acids (A) and blood glucose (B) on gestational day (GD 21) dams exposed to air (n=9), 0.4ppm ozone (n=9), or 0.8ppm ozone (n=10) on GD 5 and GD 6. The data were analyzed by two-tailed Fisher’s least significant difference (LSD) posttest within a one-way analysis of variance (ANOVA). Boxes extend from the 25th to the 75th percentile, horizontal bars represent the median, whiskers indicate the 10th and 90th percentiles, and outliers are represented as points. Values for individual dams are overlaid on each plot. * p<0.05, ** p<0.01 versus air controls.

Discussion

In this study, the offspring of Long-Evans rats with acute ozone exposure exclusively during the period of implantation receptivity had lower average fetal weight on GD 21 than air-exposed controls. Although most measures of maternal health at the end of gestation were not significantly different among treatment groups, uterine arterial resistance appeared to in-crease between GD 15 and GD 21 among dams in the high ozone–exposure group, and it appeared to decrease between GD 15 and GD 21 among dams in the control and low ozone–exposure groups, although this decrease was greater in controls. These findings suggest a relationship between maternal blood flow and fetal growth in this model. The differences in fetal body composition and in serum glucose and fatty acids in exposed dams versus controls that we observed in the present study are consistent with findings from two small case–control studies of IUGR in Italian women (Alvino et al. 2008; Larciprete et al. 2005), and they support our hypothesis that peri-implantation exposure to ozone impairs fetal growth.

Doppler ultrasonography is used to monitor uterine artery blood flow during gestation and to identify high-risk pregnancies and facilitate rapid intervention in emergency situations (Harrington et al. 1995; Sciscione et al. 2009). We used ultrasonography to monitor arterial health in vivo as a potential mechanism for the development of growth restriction. All ultrasound examiners were blinded to the treatment status of the dams they were evaluating. The prenatal environment, including both fetal development and placental adaptions, differs between males and females (Buckberry et al. 2014; Reinius and Jazin 2009). We did not formally compare differences in outcomes between male and female offspring in this study, but potential sex-specific health implications of prenatal exposures to air pollutants on the risk of adverse pregnancy outcomes present an important subject for future research.

The short duration of ozone exposure was chosen to target the timing of the receptivity window for implantation in the rat, which occurs at approximately GD 5 to GD 6.75 (Witschi 1962). The suspected origin of some adverse pregnancy outcomes, including IUGR, is impaired implantation of the blastocyst into the uterine wall (Young et al. 2010). According to accepted theory, blastocysts that do not implant at the correct depth and length can affect the ability of stem cells to form the placenta and engage in arterial remodeling. Our results suggest that implantation may be a critical time window for the effects of ambient ozone on IUGR, although we cannot rule out potential effects of exposure during other time periods. Our findings also support the value of our experimental model for the study of environmental pollutant effects on gestational outcomes in general. Epidemiological studies have reported associations between ambient air pollution exposures during early pregnancy and a variety of outcomes: for example, fetal growth parameters measured at 13–26 wk of gestation (Hansen et al. 2008), preterm birth and preeclampsia (Olsson et al. 2013), and placenta previa (Michikawa et al. 2016).

Average maternal serum FFA concentrations on GD 21 were higher in the exposed groups than in the controls in our study, consistent with findings from a case–control study reporting that serum FFAs at the time of cesarean section were higher in 24 women with IUGR pregnancies than in 30 women delivering term births by cesarean section and in 25 women at 35 wk gestation (Ortega-Senovilla et al. 2009). The higher FFAs and lowered blood glucose in exposed dams compared with controls might be related to a prolonged stress response resulting in increased lipolytic capacity as an adaptive mechanism to raise FFA availability and glucose uptake in the fetus, as has been observed in studies of pregnant ewes (Hay 2006). In the present study, we did not investigate the role of placental insufficiency in reducing fetal growth. In principle, disrupted implantation would also impair placental development. Thus, it is plausible that in this model, poor placental vascular development further compounded impaired uterine blood flow, resulting in reduced oxygen and nutrients available for development. In addition to assessing altered uterine blood flow, studies are in progress to determine if ozone exposure caused placental insufficiency and dysfunction in our model.

A previous study of mice exposed to urban air pollutants during the entirety of gestation reported that the maternal blood surface area and diameter in the placenta was reduced in exposed mice compared with controls (Veras et al. 2008). A recent study of diesel exhaust exposure throughout gestation in rabbits also reported reduced placental blood flow as measured by 3D Doppler ultrasound (Valentino et al. 2016). Relatedly, a recent prospective cohort study of 366 pregnant women reported that ambient ozone exposure during the second trimester was associated with higher umbilical artery PI (greater vascular resistance), whereas exposure during the third trimester was associated with lower PI values (Carvalho et al. 2016). Together, these studies suggest the potential for gestational exposure to air pollutants to disrupt placental function, thus contributing to impaired fetal weight gain.

In otherwise healthy Long-Evans rats, ozone exposure exclusively during implantation was not associated with significant differences in renal pathology or markers of systemic inflammation in the dams at the end of gestation. Epidemiological findings have suggested that maternal ozone exposure may induce preeclampsia (Pedersen et al. 2014), a potentially fatal pregnancy disorder. Although we did not observe any signs of preeclampsia development in ozone-exposed dams (e.g., altered blood pressure, renal changes), it is important to note that the increased uterine arterial resistance observed in rats exposed to ozone during implantation is similar to that occurring in preeclamptic pregnancies and is indicative of impaired arterial remodeling. Uterine and spiral arterial remodeling are hypothesized to contribute to the etiology of preeclampsia (Young et al. 2010).

Many of the cardiometabolic and pulmonary effects of acute ozone exposure in rodent models are believed to occur in part because of impaired respiration (Jang et al. 2003), induction of cardiac arrhythmia (Farraj et al. 2012), glucose intolerance (Bass et al. 2013), and activation of the stress response (Kodavanti 2016). Because we did not monitor all of these end points, we cannot determine whether they contributed to associations between ozone exposure and fetal growth restriction at GD 21. In addition, we could not directly observe potential mechanisms linking ozone exposure to uterine arterial changes and reduced fetal weight on GD 21, but they may be related to ozone-induced endothelial dysfunction, as previously reported (Chuang et al. 2009; Paffett et al. 2015; Robertson et al. 2013). The cardiometabolic and pulmonary effects induced by acute ozone exposure further complicate the identification of initiating mechanisms for the observed reduction in fetal weight; however, the findings presented here suggest an important interplay between the quality of implantation and alterations in arterial remodeling across gestation.

Conclusion

To our knowledge, we are the first to report experimental evidence that ozone exposure during early pregnancy may cause growth restriction in offspring. Our findings suggest that exposure during the period of implantation receptivity, which has a similar (approximately 2-d) duration in rats and humans, may cause diminished uterine artery flow later in gestation. Because 40,000,000 U.S. citizens reside in areas that are not in compliance with the NAAQS for ozone (McCarthy and Lattanzio 2015), the potential for adverse developmental consequences of ozone exposure has broad relevance for the health and well-being of infants and children.

Acknowledgments

We thank P. Dillard, R. Jaskot, A. Johnstone, J. Olin, and L. Walsh for their technical assistance, and J. Schmid for statistical support. We also thank S. Gavett, I. Gilmour, C. Gordon and M. Narotsky [U.S. Environmental Protection agency (EPA)] for their review of this manuscript. Body composition analysis was performed in part by a grant to the University of North Carolina Nutrition Obesity Research Center (DK056350, National Institute of Diabetes and Digestive and Kidney Diseases, National Institutes of Health). The research described in this article has been reviewed by the National Health and Environmental Effects Research Laboratory at the U.S. EPA and approved for publication. Approval does not signify that the contents necessarily reflect the views or policies of the agency, nor does the mention of trade names or commercial products constitute endorsement or recommendation for use.

References

Albu AR, Anca AF, Horhoianu VV, Horhoianu IA. 2014. Predictive factors for intrauterine growth restriction. J Med Life 7(2):165–171, PMID: 25408721.

Alvino G, Cozzi V, Radaelli T, Ortega H, Herrera E, Cetin I. 2008. Maternal and fetal fatty acid profile in normal and intrauterine growth restriction pregnancies with and without preeclampsia. Pediatr Res 64(6):615–620, PMID: 19034199, 10.1203/PDR.0b013e31818702a2.

Arroyo V, Díaz J, Carmona R, Ortiz C, Linares C. 2016. Impact of air pollution and temperature on adverse birth outcomes: Madrid, 2001–2009. Environ Pollut 218:1154–1161, PMID: 27589893, 10.1016/j.envpol.2016.08.069.

Bass V, Gordon CJ, Jarema KA, MacPhail RC, Cascio WE, Phillips PM, et al. 2013. Ozone induces glucose intolerance and systemic metabolic effects in young and aged Brown Norway rats. Toxicol Appl Pharmacol 273(3):551–560, PMID: 24103449, 10.1016/j.taap.2013.09.029.

Bernstein IM, Horbar JD, Badger GJ, Ohlsson A, Golan A. 2000. Morbidity and mortality among very-low-birth-weight neonates with intrauterine growth restriction. The Vermont Oxford Network. Am J Obstet Gynecol 182(1):198–206, PMID: 10649179, 10.1016/S0002-9378(00)70513-8.

Brodsky D, Christou H. 2004. Current concepts in intrauterine growth restriction. J Intensive Care Med 19(6):307–319, PMID: 15523117, 10.1177/0885066604269663.

Buckberry S, Bianco-Miotto T, Bent SJ, Dekker GA, Roberts CT. 2014. Integrative transcriptome meta-analysis reveals widespread sex-biased gene expression at the human fetal-maternal interface. Mol Hum Reprod 20(8):810–819, PMID: 24867328, 10.1093/molehr/gau035.

Carvalho MA, Bernardes LS, Hettfleisch K, Pastro LD, Vieira SE, Saldiva SR, et al. 2016. Associations of maternal personal exposure to air pollution on fetal weight and fetoplacental doppler: a prospective cohort study. Reprod Toxicol 62:9–17, PMID: 27103540, 10.1016/j.reprotox.2016.04.013.

Chuang GC, Yang Z, Westbrook DG, Pompilius M, Ballinger CA, White CR, et al. 2009. Pulmonary ozone exposure induces vascular dysfunction, mitochondrial damage, and atherogenesis. Am J Physiol Lung Cell Mol Physiol 297(2):L209–L216, PMID: 19395667, 10.1152/ajplung.00102.2009.

Cianfarani S, Agostoni C, Bedogni G, Berni Canani R, Brambilla P, Nobili V, et al. 2012. Effect of intrauterine growth retardation on liver and long-term metabolic risk. Int J Obes (Lond) 36(10):1270–1277, PMID: 22531091, 10.1038/ijo.2012.54.

Crissman JW, Goodman DG, Hildebrandt PK, Maronpot RR, Prater DA, Riley JH, et al. 2004. Best practices guideline: Toxicologic histopathology. Toxicol Pathol 32(1):126–131, PMID: 14713558, 10.1080/01926230490268756.

de Onis M, Blössner M, Villar J. 1998. Levels and patterns of intrauterine growth retardation in developing countries. Eur J Clin Nutr 52 Suppl 1:S5–15, PMID: 9511014.

Farraj AK, Hazari MS, Winsett DW, Kulukulualani A, Carll AP, Haykal-Coates N, et al. 2012. Overt and latent cardiac effects of ozone inhalation in rats: evidence for autonomic modulation and increased myocardial vulnerability. Environ Health Perspect 120(3):348–354, PMID: 22138703, 10.1289/ehp.1104244.

Frazier KS, Seely JC, Hard GC, Betton G, Burnett R, Nakatsuji S, et al. 2012. Proliferative and nonproliferative lesions of the rat and mouse urinary system. Toxicol Pathol 40(4 suppl):14S–86S, PMID: 22637735, 10.1177/0192623312438736.

Geer LA, Weedon J, Bell ML. 2012. Ambient air pollution and term birth weight in Texas from 1998 to 2004. J Air Waste Manag Assoc 62(11):1285–1295, PMID: 23210220.

Gouveia N, Bremner SA, Novaes HM. 2004. Association between ambient air pollution and birth weight in São Paulo, Brazil. J Epidemiol Community Health 58(1):11–17, PMID: 14684720, 10.1136/jech.58.1.11.

Hamelmann E, Schwarze J, Takeda K, Oshiba A, Larsen GL, Irvin CG, et al. 1997. Noninvasive measurement of airway responsiveness in allergic mice using barometric plethysmography. Am J Respir Crit Care Med 156(3 Pt 1):766–775, PMID: 9309991, 10.1164/ajrccm.156.3.9606031.

Hansen CA, Barnett AG, Pritchard G. 2008. The effect of ambient air pollution during early pregnancy on fetal ultrasonic measurements during mid-pregnancy. Environ Health Perspect 116(3):362–369, PMID: 18335104, 10.1289/ehp.10720.

Harrington K, Carpenter RG, Nguyen M, Campbell S. 1995. Changes observed in Doppler studies of the fetal circulation in pregnancies complicated by pre-eclampsia or the delivery of a small-for-gestational-age baby. I. Cross-sectional analysis. Ultrasound Obstet Gynecol 6(1):19–28, PMID: 8528796, 10.1046/j.1469-0705.1995.06010019.x.

Hatch GE, Slade R, Harris LP, McDonnell WF, Devlin RB, Koren HS, et al. 1994. Ozone dose and effect in humans and rats. A comparison using oxygen-18 labeling and bronchoalveolar lavage. Am J Respir Crit Care Med 150(3):676–683, PMID: 8087337, 10.1164/ajrccm.150.3.8087337.

Hay WW Jr. 2006. Placental-fetal glucose exchange and fetal glucose metabolism. Trans Am Clin Climatol Assoc 117:321–339, PMID: 18528484.

Jang AS, Choi IS, Kim SW, Song BC, Yeum CH, Jung JY. 2003. Airway obstruction after acute ozone exposure in BALB/c mice using barometric plethysmography. Korean J Intern Med 18(1):1–5, PMID: 12760261, 10.3904/kjim.2003.18.1.1.

Kodavanti UP. 2016. Stretching the stress boundary: linking air pollution health effects to a neurohormonal stress response. Biochim Biophys Acta 1860(12):2880–2890, PMID: 27166979, 10.1016/j.bbagen.2016.05.010.

Kramer MS. 2003. The epidemiology of adverse pregnancy outcomes: an overview. J Nutr 133(5 suppl 2):1592S–1596S, PMID: 12730473.

Lapillonne A, Peretti N, Ho PS, Claris O, Salle BL. 1997. Aetiology, morphology and body composition of infants born small for gestational age. Acta Paediatr Suppl 423:173–176, PMID: 9401567, 10.1111/j.1651-2227.1997.tb18406.x.

Larciprete G, Valensise H, Di Pierro G, Vasapollo B, Casalino B, Arduini D, et al. 2005. Intrauterine growth restriction and fetal body composition. Ultrasound Obstet Gynecol 26(3):258–262, PMID: 16116565, 10.1002/uog.1980.

Liu S, Krewski D, Shi Y, Chen Y, Burnett RT. 2007. Association between maternal exposure to ambient air pollutants during pregnancy and fetal growth restriction. J Expo Sci Environ Epidemiol 17(5):426–432, PMID: 16736056, 10.1038/sj.jes.7500503.

Liu SF, Tu DS. 2008. On the applications of Fisher’s Least Significant Difference (LSD) procedure in three-arm clinical trials with survival endpoints. Drug Inf J 42(1):81–91, 10.1177/009286150804200112.

Mattingly DK, Mcclure PA. 1982. Energetics of reproduction in large-littered cotton rats (Sigmodon hispidus). Ecology 63(1):183–195, 10.2307/1937043.

McCarthy JE, Lattanzio RK. 2015. “Ozone air quality standards: EPA’s 2015 revision.” Congressional Research Service Report. Washington, DC: Congressional Research Service. https://www.lankford.senate.gov/imo/media/doc/Ozone%20Air%20Quality%20Standards%20EPAs%202015%20Revision.pdf [accessed 12 July 2017]

Michikawa T, Morokuma S, Yamazaki S, Fukushima K, Kato K, Nitta H. 2016. Exposure to air pollutants during the early weeks of pregnancy, and placenta praevia and placenta accreta in the western part of Japan. Environ Int 92–93:464–470, PMID: 27164555, 10.1016/j.envint.2016.04.037.

Mihu D, Razvan C, Malutan A, Mihaela C. 2015. Evaluation of maternal systemic inflammatory response in preeclampsia. Taiwan J Obstet Gynecol 54(2):160–166, PMID: 25951721, 10.1016/j.tjog.2014.03.006.

Moh W, Graham JM r, Wadhawan I, Sanchez-Lara PA. 2012. Extrinsic factors influencing fetal deformations and intrauterine growth restriction. J Pregnancy 2012:750485, PMID: 22888434, 10.1155/2012/750485.

Morello-Frosch R, Jesdale BM, Sadd JL, Pastor M. 2010. Ambient air pollution exposure and full-term birth weight in California. Environ Health 9:44, PMID: 20667084, 10.1186/1476-069X-9-44.

Mose JC. 2014. The role of maternal & fetal Doppler in pre-eclampsia. Pregnancy Hypertens 4(3):242, PMID: 26104640, 10.1016/j.preghy.2014.04.010.

Murray E, Fernandes M, Fazel M, Kennedy SH, Villar J, Stein A. 2015. Differential effect of intrauterine growth restriction on childhood neurodevelopment: A systematic review. BJOG 122(8):1062–1072, PMID: 25990812, 10.1111/1471-0528.13435.

Olsson D, Mogren I, Forsberg B. 2013. Air pollution exposure in early pregnancy and adverse pregnancy outcomes: a register-based cohort study. BMJ Open 3(2):pii: e001955, PMID: 23386578, 10.1136/bmjopen-2012-001955.

Ortega-Senovilla H, Alvino G, Taricco E, Cetin I, Herrera E. 2009. Enhanced circulating retinol and non-esterified fatty acids in pregnancies complicated with intrauterine growth restriction. Clin Sci (Lond) 118(5):351–358, PMID: 19656084, 10.1042/CS20090292.

Osol G, Mandala M. 2009. Maternal uterine vascular remodeling during pregnancy. Physiology (Bethesda) 24(1):58–71, PMID: 19196652, 10.1152/physiol.00033.2008.

Paffett ML, Zychowski KE, Sheppard L, Robertson S, Weaver JM, Lucas SN, et al. 2015. Ozone inhalation impairs coronary artery dilation via intracellular oxidative stress: Evidence for serum-borne factors as drivers of systemic toxicity. Toxicol Sci 146(2):244–253, PMID: 25962394, 10.1093/toxsci/kfv093.

Pedersen M, Stayner L, Slama R, Sørensen M, Figueras F, Nieuwenhuijsen MJ, et al. 2014. Ambient air pollution and pregnancy-induced hypertensive disorders: A systematic review and meta-analysis. Hypertension 64(3):494–500, PMID: 24935943, 10.1161/HYPERTENSIONAHA.114.03545.

Peleg D, Kennedy CM, Hunter SK. 1998. Intrauterine growth restriction: identification and management. Am Fam Physician 58:453–460, PMID: 9713399.

Qu D, Adamson SL, Zhou Y-Q. 2014. Method to locate the uterine artery in mice for micro-ultrasound doppler blood velocity examination. In: The Guide to Investigation of Mouse Pregnancy. Croy BA, Yamada AT, DeMayo FJ, Adamson SL, eds. Boston: Academic Press, 693–697.

Reinius B, Jazin E. 2009. Prenatal sex differences in the human brain. Mol Psychiatry 14(11):987, 988–989, PMID: 19851278, 10.1038/mp.2009.79.

Robertson S, Colombo ES, Lucas SN, Hall PR, Febbraio M, Paffett ML, et al. 2013. CD36 mediates endothelial dysfunction downstream of circulating factors induced by O3 exposure. Toxicol Sci 134(2):304–311, PMID: 23650127, 10.1093/toxsci/kft107.

Romero A, Villamayor F, Grau MT, Sacristán A, Ortiz JA. 1992. Relationship between fetal weight and litter size in rats: application to reproductive toxicology studies. Reprod Toxicol 6(5):453–456, PMID: 1463926, 10.1016/0890-6238(92)90009-I.

Salam MT, Millstein J, Li YF, Lurmann FW, Margolis HG, Gilliland FD. 2005. Birth outcomes and prenatal exposure to ozone, carbon monoxide, and particulate matter: results from the Children’s Health Study. Environ Health Perspect 113(11):1638–1644, PMID: 16263524, 10.1289/ehp.8111.

Sankaran S, Kyle PM. 2009. Aetiology and pathogenesis of IUGR. Best Pract Res Clin Obstet Gynaecol 23(6):765–777, PMID: 19666240, 10.1016/j.bpobgyn.2009.05.003.

Sciscione AC, Hayes EJ, Society for Maternal-Fetal Medicine. 2009. Uterine artery Doppler flow studies in obstetric practice. Am J Obstet Gynecol 201(2):121–126, PMID: 19646563, 10.1016/j.ajog.2009.03.027.

Tu J, Tu W, Tedders SH. 2016. Spatial variations in the associations of term birth weight with ambient air pollution in Georgia, USA. Environ Int 92–93:146–156, PMID: 27104672, 10.1016/j.envint.2016.04.005.

U.S. EPA (U.S. Environmental Protection Agency). 2015. National ambient air quality standards for ozone EPA-HQ-OAR-2010-0885, https://www.federalregister.gov/documents/2015/10/26/2015-26594/national-ambient-air-quality-standards-for-ozone [accessed 6 November 2017]

Valentino SA, Tarrade A, Aioun J, Mourier E, Richard C, Dahirel M, et al. 2016. Maternal exposure to diluted diesel engine exhaust alters placental function and induces intergenerational effects in rabbits. Part Fibre Toxicol 13(1):39, PMID: 27460165, 10.1186/s12989-016-0151-7.

Veras MM, Damaceno-Rodrigues NR, Caldini EG, Maciel Ribeiro AA, Mayhew TM, Saldiva PH, et al. 2008. Particulate urban air pollution affects the functional morphology of mouse placenta. Biol Reprod 79(3):578–584, PMID: 18509159, 10.1095/biolreprod.108.069591.

Wallenborn JG, Schladweiler MJ, Richards JH, Kodavanti UP. 2009. Differential pulmonary and cardiac effects of pulmonary exposure to a panel of particulate matter-associated metals. Toxicol Appl Pharmacol 241(1):71–80, PMID: 19679144, 10.1016/j.taap.2009.08.003.

Witschi E. 1962. Development of the rat. In: Growth Including Reproduction and Morphological Development. Altman PL, Katz DD, eds. Washington, DC: Federation of American Societies for Experimental Biology.

Young BC, Levine RJ, Karumanchi SA. 2010. Pathogenesis of preeclampsia. Annu Rev Pathol 5:173–192, PMID: 20078220, 10.1146/annurev-pathol-121808-102149.

Zheng T, Zhang J, Sommer K, Bassig BA, Zhang X, Braun J, et al. 2016. Effects of environmental exposures on fetal and childhood growth trajectories. Ann Glob Health 82(1):41–99, PMID: 27325067, 10.1016/j.aogh.2016.01.008.



WP-Backgrounds Lite by InoPlugs Web Design and Juwelier Schönmann 1010 Wien