Skip to content


  • Research
  • Open Access

In utero exposure to ultrafine particles promotes placental stress-induced programming of renin-angiotensin system-related elements in the offspring results in altered blood pressure in adult mice

  • 1,
  • 1,
  • 3,
  • 2,
  • 1,
  • 1,
  • 4 and
  • 1Email authorView ORCID ID profile
Particle and Fibre Toxicology201916:7

  • Received: 12 October 2018
  • Accepted: 13 January 2019
  • Published:



Exposure to particulate matter (PM) is associated with an adverse intrauterine environment, which can promote adult cardiovascular disease (CVD) risk. Ultrafine particles (UFP) (small size and large surface area/mass ratio) are systemically distributed, induce inflammation and oxidative stress, and have been associated with vascular endothelial dysfunction and arterial vasoconstriction, increasing hypertension risk. Placental stress and alterations in methylation of promoter regions of renin-angiotensin system (RAS)-related elements could be involved in UFP exposure-related programming of hypertension. We investigated whether in utero UFP exposure promotes placental stress by inflammation and oxidative stress, alterations in hydroxysteroid dehydrogenase 11b-type 2 (HSD11B2) and programming of RAS-related elements, and result in altered blood pressure in adult offspring. UFP were collected from ambient air using an aerosol concentrator and physicochemically characterized. Pregnant C57BL/6J pun/pun female mice were exposed to collected UFP (400 μg/kg accumulated dose) by intratracheal instillation and compared to control (nonexposed) and sterile H2O (vehicle) exposed mice. Embryo reabsorption and placental stress by measurement of the uterus, placental and fetal weights, dam serum and fetal cortisol, placental HSD11B2 DNA methylation and protein levels, were evaluated. Polycyclic aromatic hydrocarbon (PAH) biotransformation (CYP1A1 and NQO1 (NAD(P)H dehydrogenase (quinone)1)) enzymes, inflammation and oxidative stress in placentas and fetuses were measured. Postnatal day (PND) 50 in male offspring blood pressure was measured. Methylation and protein expression of (RAS)-related elements, angiotensin II receptor type 1 (AT1R) and angiotensin I-converting enzyme (ACE) in fetuses and lungs of PND 50 male offspring were also assessed.


In utero UFP exposure induced placental stress as indicated by an increase in embryo reabsorption, decreases in the uterus, placental, and fetal weights, and HSD11B2 hypermethylation and protein downregulation. In utero UFP exposure induced increases in the PAH-biotransforming enzymes, intrauterine oxidative damage and inflammation and stimulated programming and activation of AT1R and ACE, which resulted in increased blood pressure in the PND 50 male offspring.


In utero UFP exposure promotes placental stress through inflammation and oxidative stress, and programs RAS-related elements that result in altered blood pressure in the offspring. Exposure to UFP during fetal development could influence susceptibility to CVD in adulthood.


  • Ultrafine particles
  • Placental stress
  • Programming disease
  • Hypertension


Exposure to airborne particulate matter (PM10 and PM2.5) is associated with increased morbidity and mortality due to cardiovascular disease (CVD) [1, 2]. Furthermore, cardiovascular mortality from air pollution exposure could be mediated by elevated blood pressure [3]. Airborne PM includes ultrafine particles (UFP), with an aerodynamic diameter of < 0.1 μm and a high surface area to mass ratio. However, few studies have included them as a dependent factor [4] because there are no air quality regulations that address the UFP, and this class of particles is not considered to be part of the pollutants routinely monitored to assess air quality (i.e., criteria pollutants). Experimental evidence suggests that UFP may exert a higher relative toxicity than PM10 and PM2.5, because of their small size, large surface area/mass ratio, chemical composition, capacity to generate reactive oxygen species (ROS), high retention rate, penetration into deep regions of the lung, and their ability to translocate to the systemic circulation [5].

Epidemiologic and experimental studies have reported that the effects of PM exposure in adulthood may be temporary. The developmental plasticity allows the fetus to adapt to an adverse intrauterine environment, such as that induced by air pollution [6]. Several epidemiological studies have shown that exposure to PM during pregnancy is associated with detrimental developmental outcomes, such as low birth weight [7], preterm birth, and intrauterine growth restriction [8]. Interestingly, reduced birth weight has been associated with the susceptibility to hypertension [9]. Alterations in the fetal development and dysfunctional placentas have been consistently observed in experimental models of in utero exposure to PM2.5 [10], diesel exhaust particles (DEP) [11], or nanoparticles [12, 13] in animal models. These effects have been accompanied with intrauterine (fetus and placenta) inflammation and oxidative damage. This could be due to the direct or indirect effects of the UFP. The direct effects refer to conditions in which particles or their components, such as polycyclic aromatic hydrocarbon (PAH) and metals, traverse first the pulmonary and subsequently the placental barrier and reach the fetus, where their oxidative and inflammatory effects directly impact the fetal tissues. In contrast, the indirect effects may occur after inhaled UFP deposit in the maternal alveoli and generate ROS through their reactivity, the product of the biotransformation of PAH or any other intrinsic compounds contained in UFP, which result in oxidative stress and inflammation. The inflamed lung tissue releases inflammatory mediators (e.g., cytokines) to the bloodstream, which can reach other organs and intrauterine tissues [14]. Among the biological tools available to evaluate a transplacental exposure to pollutants is the transgenic mouse model C57BL6/6Jpun/pun strain [15], which expresses visible mutations of DNA caused by the deletion of DNA sequences in the embryo. Studies have reported a significant increase in the frequency of DNA deletions of the pun gene in the mouse fetus, when pregnant dams were exposed to xenobiotics (DEP, TiO2 nanoparticles and TCDD [1618]).

Recently, Niu et al. showed an association between the exposure to PM2.5 and the activation of the HPA axis [19]. The hypothalamic–pituitary–adrenal (HPA) axis regulates the production and secretion of glucocorticoids such as cortisol and corticosterone under basal and stress conditions. Excessive levels of glucocorticoids during fetal development may contribute to cardiovascular programming [20]. To protect the developing fetus from the deleterious effects of an excess of glucocorticoids, the placental enzyme HSD11B2 inactivates the glucocorticoids cortisol/corticosterone by converting them into the inactive metabolites cortisone/11b-dehydrocorticosterone [21]. Interestingly, in utero exposure to PM10 is associated with methylation of the promoter region of HSD11B2 [22], and furthermore, a decrease of mRNA expression and hypermethylation of the promoter region of HSD11B2 can be induced by inflammatory mediators [23] and prenatal stress [24], respectively. DNA methylation is a process that is catalyzed by the DNA methyltransferases (DNMTs), and generally, under-methylation is associated with transcription and over-expression of proteins and a hypermethylation is associated with transcriptional repression [25]. This suggests that a dysfunctional placental environment may contribute to adult cardiovascular programming, although the mechanisms of the developmental programming are not well understood.

The RAS plays a central role in the control of blood pressure and is one of the most critical steps in the pathogenesis of hypertension. The RAS components angiotensin-converting enzyme (ACE) catalyzes the conversion of the inactive decapeptide angiotensin I (Ang-I) to the active octapeptide angiotensin II (Ang-II). The action of Ang-II results from the binding to its specific receptor (AT1R), which mediates the vasoconstrictor response [26]. In rodents, AT1R exists as two distinct subtypes, AT1a and AT1b receptor (encoded by Agtr1a and Agtr1b respectively) [27]. The RAS is overexpressed during pathological cardiovascular states, such as hypertension, atherosclerosis, heart infarction, and heart failure. Moreover, in animal models, DNA hypomethylation in the promoter regions of Agtr1b, Agtr1a and ACE was also found to be correlated with hypertension [28, 29]; those studies strongly support the consequence of epigenetic modification of the hypertension programming. In addition, we have previously demonstrated that the exposure to PM (PM2.5 and UFP) induces the expression of RAS elements, including AT1R in lungs and heart [30]. Likewise, Gunnison and Chen observed a 1.5-fold increase in the differential expression of At1r in a lung microarray of double-knockout mice (apoE −/− and LDLr−/−) that were subchronically exposed to UFP [31].

We hypothesized that in utero exposure to UFP can promote placental stress that would result in adverse intrauterine conditions, which leads to programming hypertension from the activation of RAS-related elements. In addition, we report that in utero exposure to UFP promotes an adverse intrauterine environment that results in the susceptibility to hypertension in PND 50 male offspring.


Collection and physicochemical characterization of UFP

Ultrafine particles from the air of Mexico City (northern region) were collected from April to June of 2016, 5 days/week, 5 h/day (7 am - 12 pm). We used an aerosol enrichment concentrator system [32] that drew air samples that contained airborne particles through two parallel lines using > 0.25 μm cut point preimpactors to remove larger size particles. These particles are drawn through a saturation-condensation system that grows particles to 2–3 μm droplets, which are subsequently concentrated by virtual impaction. Concentrated particle suspensions were obtained by connecting the aerosol enrichment concentrator system output to a sterilized liquid impinger (BioSamplers™, SKC West, Inc., Fullerton, CA, USA) that contained ultrapure and sterile water as the collection medium. The concentration enrichment process does not alter the physical, chemical, and morphologic properties of the particles [32]. Samples from 10-weeks were pooled and stored at − 70 °C until analysis and animal exposure. We determined UFP concentration in the suspension by gravimetric analysis as previously described [33]. Briefly, after sonication of the particle suspension of the concentrated pooled sample, 50 μl aliquots were placed on sterile aluminum cuvettes to let the water evaporate during 2–4 days under constant 45% humidity and 30 °C temperature conditions. The aluminum cuvettes were weighted before and after evaporation in a microbalance to determine the mass of UFP in the suspension (used for UFP analysis and animal instillations).

We used scanning and transmission electron microscopy to assess the particle morphology and size distribution. A small drop of the particle suspension was placed on nonporous carbon tape or Lacey Formvar/carbon grid for analysis using a scanning electron microscope (SEM, Auriga 3916, Carl Zeiss) or transmission electron microscope (TEM, JEOL, JEM-ARM200F), respectively. UFP samples collected in the parallel concentrator system output using quartz were used to quantify their carbon, metal and PAH content. Elemental and organic carbon was determined by the coulombimetry method as previously described [34]. The elemental composition was analyzed using X-ray fluorescence (XRF). The X-ray detector was an Amptek (Bedford, MA, USA). The PAH species were analyzed in a gas chromatograph/mass spectrometer (6890/5973 N) (Agilent Technologies, Little Falls, CA, USA) with a quadrupole mass filter and an autosampler (model 7683). Further characterization of the UFP included hydrodynamic size (DH) (aggregation state of the UFP) and polydispersity index (PDI) (the broadness of the size distribution). We conducted the analysis using dynamic light scattering and Zeta potential (ζ) (dispersion stability) with laser Doppler microelectrophoresis. Both techniques were performed using a Zetasizer Nano ZS90 size analyzer (Malvern Instruments, Malvern, UK). The suspensions of the UFP concentrated pooled samples were sonicated for 5 min before use. The oxidative potential of UFP was measured on the basis of dithiothreitol (DTT) consumption as previously described in detail elsewhere [35].

Animals and UFP in utero exposure

Male and female C57BL/6J pun/pun mice were kindly donated by Dr. Robert Schiestl from University of California, Los Angeles. All mice were housed in a freestanding clean room with a changing station docking port (bioBubble®, Fort Collins, Co., USA) on a 12/12 light/dark cycle in the animal facility at Cinvestav according to the institutional guidelines. All animal procedures were approved by the Internal Committee for the Use and Care of Laboratory Animals in accordance to the “Principles of Laboratory Animal Care” guidelines. Six-week-old females in estrus stage (determined by vaginal cytology as described in [36]) were mated, and the weight was monitored [37]. Once pregnancy was confirmed, each dam was housed in a separate cage until offspring birth, which remained with the dam until after weaning. The pregnant mice were exposed by intratracheal instillation as previously described in [38]. The dams were anesthetized with 4% isoflurane and instilled through the trachea with the UFP suspension (50 μl followed by 200 μl air) for the UFP exposed group (n = 4). For the H2O group, dams (n = 4) were instilled with sterile ultrapure water (50 μl followed by 200 μl air). A non-exposed group (no UFP, no H2O) was included as a control group (CTRL) (n = 4). The instillations were repeated six times during the fetal development after implantation on gestation day (GD) 6.5, 8.5, 10.5, 12.5, 14.5 and 16.5 day of pregnancy. The total dose per animal was 12 μg or 400 μg/kg (Fig. 1).
Fig. 1
Fig. 1

Experimental design of animal UFP exposure and sample collection. GD, Gestation day (pregnancy day); PND, post natal day (days after birth). Time mated mice were exposed by intratracheal instillation to H2O and UFP. The instilled dose was 12 μg/dam was distributed over six instillations on GD 6.5, 8.5,10.5, 12.5,14.5 and 16.5

Tissue collection

On GD 17.5, after the last UFP instillation, the dams were anesthetized with 4% isoflurane and euthanized by cervical dislocation. For the prenatal study, the uterus (n = 4 per group) of each dam was collected, and visual evaluation was carried out to detect and quantify embryo reabsorption and to evaluate the fetal and placental effects of the in utero exposure to UFP. After removal of the uterus (that included placenta, amnion, fetus, and membranes), placentas and fetuses were weighed, analyzed for weight difference and averaged per litter. The fetuses and placentas were quick-frozen in liquid nitrogen and stored at − 70 °C until analysis. To perform the placenta and fetus analyses of biotransformation enzymes, oxidative damage, and HSD11B2 methylation and protein levels in (n = 6 per group), both tissues were mixed and randomly selected (see the sex ratio Additional file 1: Table S2). Also, the lung and total blood of dams (obtained by cardiac puncture) were obtained to evaluate biotransformation enzyme, serum cortisol and systemic inflammation. For postnatal analysis (n = 6 per group), dams were exposed as described previously, and they were allowed to deliver spontaneously. The total litter size and the number of live pups were recorded on postnatal day 0 (PND 0). On PND 21 or after weaning, the offspring were euthanized. Their eyes were extracted for retinal pigment epithelium (RPE) test; we analyzed 15 pairs of eyes of 15 (30 eyes per group), regardless of offspring sex. Only male offspring were allowed to grow into 50 PND to measure the blood pressure, collect the lungs for methylation analysis and protein levels of RAS-related elements (n = 4 per group). Our study focused on male offspring to control for cyclic hormonal variation. The placentas and fetuses were mixed and randomly selected for analysis.

Deletion/eyespot assay in p un mice

To evaluate the transplacental in vivo exposure we used a homozygous mouse model (C57BL/6J pun/pun), taking advantage of the p (un) allele (pink-eyed unstable), which contains a tandem duplication of a 70-kb fragment spanning exons 6 to 18 of the p gene in mice. Mice with the p (un) allele have a transparent RPE. A deletion of these duplications induced by the exposure to xenobiotics restores the p gene, which encodes a protein responsible for the assembly of a black-colored melanin complex that will produce black pigmented cells (eye-spots) in the offspring. The eyes extracted from the weaned offspring were dissected to display the RPE for the deletion/eyespot assay as described previously in [39].

Serum and fetus cortisol determination

Mice and rats, which are nocturnal, are commonly used in glucocorticoid research, and exhibit an inverse tempo in glucocorticoid profile, with peak plasma levels of corticosterone and cortisol at night and decreased concentrations during the day [40]. Also, although corticosterone is the main glucocorticoid involved in the regulation of stress responses in rodents, several studies have shown increased cortisol levels in plasma and adrenal glands of mice following environmental stress [41, 42]. For these reasons and to minimize serum cortisol variations, dams were always euthanized during the day (between 11:00 am and 2:00 pm), and cortisol was chosen over corticosterone to determine glucocorticoid levels. To evaluate the placental dysfunction and activation of the hypothalamic pituitary adrenal axis (HPA) induced by the in utero exposure to UFP, the cortisol levels of the homogenized fetuses and dam sera were measured using a Mouse/Rat cortisol ELISA kit (Sigma-Aldrich, Poole, Dorset UK) following the manufacturer’s instructions. To obtain the total protein, the whole fetuses were homogenized with Nonidet-P40 buffer (150 mM NaCl, 1% NP40, 50 mM Tris–HCl, pH 8.0, and protease inhibitors) and centrifuged at 10,000 rpm/4 °C, and the supernatant was collected.

Detection of placental and fetus 8-OH-dG

The levels of 8-hydroxydeoxyguanosine (8-OHdG) were assessed in the placental and fetal DNA to evaluate the oxidative damage produced by the UFP. The DNAzol reagent (Molecular Research Center, Cincinnati, OH, USA) was used to isolate genomic DNA of whole placentas and fetuses (as previously described). An 8-OH-dG ELISA kit (Cayman Chemical, Ann Arbor, MI, USA) was used, and all procedures were conducted according to the manufacturer’s instructions.

Analysis of cytokines and chemokines

The pro-inflammatory cytokines interleukin-β (IL-β), IL-6 and tumor necrosis factor-α (TNF-α), the anti-inflammatory cytokines IL-10 and IL-4, chemokines including neutrophil chemoattractant (KC), macrophage inflammatory protein 2 (MIP-2) and monocyte chemoattractant protein 1 (MCP-1), and vascular endothelial growth factor (VEGF) were measured in the dam sera and the total protein of the dam lungs, placentas and fetuses using an MCYTOMAG-70 K Milliplex MAP Mouse Cytokine/Chemokine magnetic bead panel (EMD Millipore, Billerica, MA, USA) following the manufacturer’s instructions.

Western blot

Frozen tissues were homogenized in Nonidet-P40 buffer as described above to extract the total protein. The protein was quantified using the Bradford protein assay, then 30 μg of the protein was electrophoresed (SDS-PAGE), and then transferred to nitrocellulose membranes. The membranes were blocked for 1 h with 5% of not-fat milk in PBS. The membranes were then incubated overnight with the primary antibodies to HSD11B2 (1:300; rabbit polyclonal, ab115696, Abcam, Cambridge, MA, USA), NQAO1 (1:500; rabbit polyclonal, ab34173, Abcam), AT1R (1:500; rabbit polyclonal, Sc-579, Santa Cruz Biotechnology, Santa Cruz, CA, USA), ACE (1:1000; goat polyclonal, Sc-12,184, Santa Cruz Biotechnology) or CYP1A1 (1:500; mouse polyclonal, Sc-253,041, Santa Cruz Biotechnology), and GAPDH (1:1000, mouse monoclonal, Sc-32,233, Santa Cruz Biotechnology) was used as a loading control. Horseradish peroxidase (HRP)-conjugated secondary antibody (1:10000; Bio-Rad Laboratories, Hercules, CA, USA) was incubated with the membranes at room temperature for 1 h, and the HRP was subsequently detected using the Luminata Forte Western HRP substrate reagent (Millipore, Burlington, MA, USA). The expression levels were visualized by exposure to X-ray film and quantified by optical densitometry, using the ImageJ software (free from the National Institutes of Health).

DNA methylation analysis

Placentas, fetuses, and lung samples of the male offspring at PND 50 were obtained, and the DNA was extracted and purified using the Genomic DNA Purification Kit (DNeasy blood and tissue, Qiagen, Hilden, Germany). Bisulfite conversion was performed on 1 μg of genomic DNA using the EZ-96 DNA methylation kit (Zymo Research, Orange, CA, USA) according to the manufacturer’s instructions. Tissue-gene specific methylation in the promoter region was assessed for HSD11B (9 CpG sites), Ace (7 CpG sites), Agtr1a (4 CpG sites), and Agtr1b (5 CpG sites) genes. The primer design was focused on CpG dinucleotides located in the CpG island closest to the transcription start site (TSS), on the basis that H3K27Ac indicates as high a probability of transcription factor binding as CTCF. Polymorphisms and repetitive elements were avoided, and the UCSC database and MethPrimer tool were used [43, 44]. DNA methylation of Ace, Agtr1a and Agtr1b was analyzed in fetal samples and those from the lungs of the male offspring at PND 50, and methylation of HSD11B gene was evaluated in the placenta. After bisulfite treatment, the samples were amplified by PCR. A 30-μl PCR was carried out using 15 μl of GoTaq Hot Start Green Master Mix (Promega, Madison, WI, USA) with 10 pmol of each primer (Sigma Aldrich) and 1 μl of the bisulfite-treated DNA. The PCR and sequencing primers are shown in Additional file 2: Table S1. Two sequencing primers were used to analyze the total CpG sites for HSD11B and ACE. Pyrosequencing analysis was done using the PyroMark® Q24 Pyrosequencing System with PyroMark Gold reagents (Qiagen, Hilde, Germany) according to the manufacturer’s instructions. PyroMark® Control Oligo, which contains 50% 5-mC and 50% cytosine, was used. In addition, several thymine residues were intentionally added as controls to verify the bisulfite conversion of each run. The samples were run in duplicate. The methylation values were quantified using the PyroMark® Analysis software version 2.0.7 (Qiagen, Hilde, Germany). The output from pyrosequencing analysis is reported as a percent of 5-methylcytosine (% 5-mC) at each CpG site.

Blood pressure

Blood pressure was measured in the male offspring at PND 50 using the tail-cuff pressure system (Digital pressure meter LE 5002 LETICA, Panlab, S.L. Barcelona, Spain). The mice were acclimated to the restraint and warm-up procedures during the week before the blood pressure measurements. During the acclimation days, the male mice were placed into a restraining tube used for the tail-cuff and warmed-up in a hot chamber at 35 °C for 10 min to vasodilate the blood vessels. After the acclimatization period, the mice were restrained and preheated for 10 min, after which the blood pressure was measured using a fitted cuff with a pneumatic pulse sensor. At least ten consecutive blood pressure values were recorded per mouse and averaged.

Statistical analysis

All data are expressed as the means ± SEM or SD. One-way or two-way ANOVA with Tukey’s posthoc test was used to perform the statistical tests. Only for the analysis of the number of dams with resorbed embryo and number of resorbed embryos the Student’s t-test was performed. The results were considered statistically significant at p < 0.05. GraphPad Prism (GraphPad Software, San Diego, CA, USA) was used for the statistical analysis.


Physicochemical characterization of the collected UFP

Ultrafine particles collected from the air pollution were characterized dry and in suspension (distilled, sterilized water) (Fig. 2a-c and Table 1). Observations by transmission electron microscopy and scanning electron microscopy showed that the UFP possessed diameters smaller than 60 nm and had a rounded shape. When suspended in H2O, the particles demonstrated a hydrodynamic diameter of 94 nm, a polydispersity index of 0.632 and a Zeta potential of 28 mV, which indicated a stable dispersion in H2O. The UFP suspension showed a high redox potential (0.174 nmol DTT/min*μg). Measurements of the UFP suspension mass by gravimetrical analysis showed a concentration of 2 μg of particles in 50 μl of suspension. The UFP chemical composition was 42.55% organic carbon (OC), 14.46% elemental carbon (EC), < 1% metals, and 42.19% other compounds (Fig. 2 d). The most abundant metals were Fe, K, Ca, Cr, Ni, Zn, Cu and Ti, and the most abundant PAH species were naphthalene, phenanthrene and benzo[a]pyrene (Table 2).
Fig. 2
Fig. 2

Physicochemical characterization of UFP. The geometric size was determined by a) TEM imaging, b) the frequency of the size distribution of UFP, c) SEM imaging, and d) fractional composition of the UFP collected

Table 1

Characterization of UFP dispersion in H2O

DH (nm)


ζ (mV)

Redox potential (nmolDTT/min*μg)

94 ± 8.65

0.632 ± 0.17

28 ± 0.03

0.174 ± 0.002

DH: Hydrodynamic diameter. PDI: Polydispersion index. ζ: zeta potential. DTT: Dithiothreitol

The UFP pool in H2O at 40 μg/ml, were analyzed in triplicate. Values represent mean ± SEM

Table 2

Chemical composition of UFP. Values are representative of n = 6 filters and are given as ng/μg of UFP






± 10.383



± 8.703



± 9.086



± 1.589



± 10.242



± 29.497



± 13.757



± 20.957

PAH species





± 2.703



± 2.206



± 2.465



± 3.600



± 1.532



± 1.284



± 0.630



± 0.887

 Benzo [a] anthracene


± 0.511



± 0.933

 Cyclopenta [c, d] pyrene


± 0.703



± 0.170

 Benzo [b] fluoranthene


± 0.875

 Benzo [k] fluoranthene


± 0.581

 Benzo [j] fluoranthene


± 0.492

 Dibenzo [a, e] pyrene


± 0.071

 Benzo [e] pyrene


± 1.002

 Benzo [a] pyrene


± 1.497

 Indeno[1,2,3-cd] pyrene


± 0.606

 Benzo [ghi] perylene


± 1.022

Transplacental in vivo UFP exposure does not induce DNA deletion

The deletion/eyespot assay in C57BL/6J pun/pun mice was used to evaluate deletion events as a result of the transplacental in vivo UFP exposure. The numbers of eyespots or DNA deletions per RPE of weaning offspring were quantified (Table 3). The UFP-treated mice showed 1.9 ± 0.16 eyespots per pup, and there were 1.7 ± 0.17 in the H2O-exposed mice and 1.4 ± 0.13 in the CTRL mice. There were no significant differences among the groups. Therefore, in utero UFP exposure did not induce an increase in DNA deletions in RPE in the pun model.
Table 3

Frequency of DNA deletions as an evaluation of transplacental in vivo UFP exposure


No. RPEa

Average number of eye-spots per RPE ± SEM

Average number of cells per eye-spot ± SEM



4.9 ± 0.17

2.3 ± 0.14



4.6 ± 0.13

1.9 ± 0.40



5.1 ± 0.16

2.1 ± 0.09

aOne RPE corresponds to one eye

In utero UFP exposure induces embryonic reabsorptions and decreases fetal and extraembryonic tissue weight

Table 4 shows the dam weights measured at GD 17.5; a significant decrease in the body weight gains of the dams that were exposed to UFP was observed compared to the H2O-exposed and CTRL groups. Each uterus was extracted and examined for embryo reabsorptions, and we identified a significant increase in the number of dams with resorbed embryos as well as in the number of resorbed embryos per mouse after the exposure to UFP compared to H2O-exposed and CTRL groups. The individual placentas and fetuses were weighed, and their weights were significantly lower in mice that were exposed to UFP compared to the H2O-exposed and CTRL groups. Another group of dams delivered spontaneously (PND 0) and the total litter size was significantly decreased after the UFP exposure versus the H2O-exposed and CTRL groups.
Table 4

Embryonic resorptions, fetal and extra-embryonic tissues weight


CTRL (n = 4)

H2O (n = 4)

UFP (n = 4)

Litter size (mean ± SEM)

7.25 ± 0.47

8.50 ± 0.64

5.50 ± 0.69*

 No. dams with resorbed embryo




 No. resorbed embryo




 Dam weight on GD 17.5 (g)

 (mean ± SEM)

34.3 ± 0.90

35.73 ± 1.63

32.7 ± 0.76*

Uterus weight on GD 17.5 (g)

(mean ± SEM)

9.59 ± 0.48

10.33 ± 0.80

7.98 ± 0.81

Fetus weight on GD 17.5 (g)

(mean ± SEM)

0.90 ± 0.02

0.94 ± 0.05

0.79 ± 0.04*

Placenta weight on GD 17.5 (g)

(mean ± SEM)

0.14 ± 0.003

0.14 ± 0.001

0.12 ± 0.001*

* Statistically significant difference compared to the control and H2O group * p < 0.05. One-way ANOVA

+ Statistically significant difference compared to the control and H2O group + p < 0.05 and ++ p < 0.05. T-Student

Table 5

Blood pressure in male 50 PND offspring


CTRL (n = 6)

H2O (n = 6)

UFP (n = 6)

SAP (mm Hg)

136.6 ± 3.12

141.9 ± 5.36

156.4 ± 3.90 *

DAP (mm Hg)

109.1 ± 3.33

106.7 ± 7.54

124.2 ± 2.80*

MAP (mm Hg)

116.0 ± 3.35

110.1 ± 6.98

133.9 ± 4.77*

HR (bts/min)

614.4 ± 18.24

608.4 ± 30.88

614.8 ± 21.10

Mean ± SEM of values of systolic arterial pressure (SAP), diastolic arterial pressure (DAP), mean arterial pressure (MAP) and heart rate.

* Statistically significant difference compared to the control and H2O group * p < 0.05. One-way ANOVA

In utero exposure to UFP induces placental dysfunction modulation and promotes activation of hypothalamic-pituitary-adrenal axis (HPA)

To evaluate the effect on placental stress that was caused by in utero exposure to UFP, we measured the protein levels and methylation of the promoter region of HSD11B2 (Fig. 3a and b). The protein level of HSD11B2 was statistically lower in the placentas from dams that were exposed to UFP compared to the H2O-exposed and CTRL groups. Likewise, the methylation of 9 CpG sites of its promoter region was evaluated by pyrosequencing. A significant increase in the %5-mC in the first and ninth CpG sites was observed in the placentas of the dams that were exposed to UFP compared to the H2O-exposed and CTRL groups. In contrast, in the fifth CpG site, a significant decrease in the %5-mC was observed in the UFP-exposed group compared to both control groups. In addition, the mean of the %5-mC in all CpG sites was not different among groups.
Fig. 3
Fig. 3

In utero exposure to UFP induces placental dysfunction and promotes activation of hypothalamic pituitary adrenal axis (HPA). a Protein levels and representative image of Western blot of placenta HSD11B2. n = 6/group; * p < 0.05. One-way ANOVA. b DNA methylation of the HSD11B2 promoter in placenta determined by pyrosequencing. n = 4/group; * p < 0.05. Two-way ANOVA. c Dam serum cortisol and d fetus cortisol were determined by ELISA. n = 4/group. Data are expressed as mean ± SEM. *p < 0.05 and ** p < 0.01. One-way ANOVA

On the other hand, several studies have suggested that the HPA may play a critical role in developmental programming [20]. To evaluate whether HPA activation in pregnant dams that were exposed to UFP promoted a deficit in placental HSD11B2, we measured the levels of cortisol in the dam and fetal serum on GD 17.5. Figure 3 c and d show that in utero exposure to UFP significantly increased the serum cortisol levels in the dams and fetuses compared to the respective control groups.

In utero exposure to UFP induces oxidant damage

The ultrafine particles have higher redox activity than larger particles due in part to their high content of organic compounds such as PAH. These compounds induce oxidative stress through their biotransformation by the cytochrome P450 CYP1A1 isoform and NQO1. This process generates redox-active quinones, which can lead to the formation of 8-hydroxydeoxyguanosine (8-OHdG). Therefore, we investigated whether in utero UFP exposure promoted oxidative damage to the placentas and fetuses through the PAH metabolism. ELISAs were used to measure the levels of 8-OHdG in the placentas and fetuses (Fig. 4a and b) as a marker of oxidative damage. The in utero UFP exposure promoted oxidative damage as indicated by a significant increase in 8-OHdG in both in placentas and fetuses. The CYP1A1 and NQO1 protein levels significantly increased in both the dam lungs and placentas in the UFP-exposed group compared with the control groups (Fig. 4c and d).
Fig. 4
Fig. 4

In utero exposure to UFP induces oxidant damage by metabolism of PAHs. Levels of 8-hydroxydeoxyguanosine (8-OHdG) were measured by ELISA in a) placenta and b) fetus. n = 4/group; * p < 0.05 and ** p < 0.01. One-way ANOVA. c Protein levels and representative image of Western blot of dam lung CYP1A1 and NQO1, and d) placental CYP1A1 and NQO1. n = 4/group. Data are expressed as mean ± SEM. * p < 0.05 and ** p < 0.01. One-way ANOVA

In utero exposure to UFP induces systemic and intrauterine inflammation

To determine whether in utero UFP exposure induced systemic and intrauterine inflammation, pro-inflammatory and anti-inflammatory cytokines and chemokines were measured in dam serum, dam lung, placenta and fetus total protein. All studied cytokines and chemokines were detected in dam lungs (Fig. 5a), and elevated concentrations of IL-β, IL-6, IL-4 KC, MCP-1 and MIP-2 were observed in the UFP-exposed group. Furthermore, in the dam sera (Fig. 5b) only IL-1β, IL-6 and MCP-1 were found to be increased in the UFP-exposed group (Fig. 5b). On the other hand, increased levels of IL-6 and KC were consistently induced by in utero UFP exposure in the placentas and fetuses (Fig. 5c and d). Conversely, fetal VEFG showed a significant decrease.
Fig. 5
Fig. 5

In utero exposure to UFP induces systemic and intrauterine inflammation. Concentrations of pro-inflammatory cytokine: interleukin-β (IL-β), IL-6 and tumor necrosis factor-α (TNF-α). The anti-inflammatory cytokines IL-10 and IL-4. Chemokines: neutrophil chemoattractant (KC), macrophage inflammatory protein 2 (MIP-2) and monocyte chemoattractant protein 1 (MCP-1). Vascular endothelial growth factor (VEGF) ware measured with multiplex magnetic beads in a) dam serum collected, b) dam lung, c) placenta and d) fetus total protein. n = 4/group. Data are expressed as mean ± SEM. *p < 0.05, ** p < 0.01 and *** p < 0.001. One-way ANOVA

In utero exposure to UFP induces cardiovascular programming by DNA hypomethylation of RAS-related elements AT1a, AT1b receptor and ACE promoters in the fetuses and lungs of the male offspring AT PND 50

Fetal programming of hypertension could be mediated by an epigenetic mechanism, through DNA methylation of the promoter region. RAS has been implicated in the pathogenesis of hypertension. Furthermore, components of RAS, similar to the angiotensin receptors Agtr1a and Agtr1a, and Ace are subjected to methylation [28, 29]. Therefore, to evaluate whether in utero UFP exposure induced changes in the methylation pattern in the promoter regions of the RAS genes, we assessed the percent of 5-mC at each CpG site in the promoter regions of Agtr1a, Agtr1b and Ace genes of the fetuses and lungs of the male offspring at 50 PND. Five CpG sites were evaluated for the Agtr1a promoter region, and a significant difference in the third CpG site was observed in the UFP-exposed fetuses (Fig. 6a) whereas in the lungs of the male offspring at PND 50 (Fig. 6b), a significant change was observed in the first CpG. The percent of 5-mC in the second CpG site of the Agtr1b promoter region was significantly lower in the fetuses (Fig. 6c) as well as in the lungs of the male offspring at PND 50 (Fig. 6d) in the UFP-exposed mice compared with the H2O-exposed and CRL groups. Additionally, Fig. 6d exhibited that in utero UFP exposure significantly decreased the average methylation of all sites in the lungs of the male offspring at PND 50. Of the 7 CpG sites analyzed in the Ace promotor region, only the seventh and second CpG sites were significantly lower in the fetuses and lungs of the male offspring at PND 50 (Fig. 6e and f), respectively, in UFP-treated animals compared with both control groups.
Fig. 6
Fig. 6

In utero exposure to UFP induces cardiovascular programming by DNA hypomethylation of the Agtr1a, Agtr1b and ACE promoter in fetus and adult lung. Percentage of methylated 5 CpG sites in Agtr1a, Agtr1b and ACE promoter in the a, c and e) fetus and b, d and f) lung. n = 4/group; *p < 0.05, **p < 0.01 and *** p < 0.001. Two-way ANOVA. c Protein levels and representative image of Western blot of G) fetus AT1R and H) ACE, and I) lung AT1 and ACE. n = 4/group. Data are expressed as mean ± SEM. * p < 0.05 and ** p < 0.01. One-way ANOVA

Hypomethylation is associated with transcriptional activation and the overexpression of proteins. To confirm these changes, we assessed the protein levels of AT1R and ACE in the fetuses and lungs of the male offspring at PND 50 by western blotting. We used an antibody that recognizes both AT1a and AT1b receptors, which are highly homologous (95% identical in their amino acid sequences) [45]. In the fetuses, significant increases in AT1R and ACE were induced by the in utero UFP exposure (Fig. 6g and h). Additionally, significant differences were observed in the AT1R and ACE protein levels in the lungs of the male offspring at PND 50 in the in utero UFP exposed groups compared with the H2O-exposed and CTRL groups.

In utero exposure to UFP promotes altered blood pressure in the male offspring at PND 50

We investigated whether in utero UFP exposure induced long-term effects on blood pressure in offspring at PND 50 (Table 5). Systolic and mean arterial pressure were statistically increased in the offspring male exposed in utero to UFP compared to both control groups whereas the diastolic pressure was significantly higher only compared with the CTRL group. No significant differences were observed in the heart rate.


There is substantial evidence that intrauterine stress induced by environmental stressors may program the later development of diseases. Of special interest for this study was the association of cardiovascular disease-hypertension with exposure to ambient PM. Experimental evidence suggests that UFP could pose a greater risk to human health than PM10 and PM2.5, given their smaller size, large surface area/mass ratio, and increased reactivity. We, therefore, developed a stable dispersion of the UFP to expose pregnant mice through intratracheal instillation. Our results indicate that the exposure to UFP during fetal development (12 μg/animal or 400 μg /kg) promoted placental stress and gene programming associated with toxicological factors of mouse hypertension. In this study, we exposed to 12 μg of UFP per dam, distributed every 2 days 6 times during the fetal development stage. The exposure of 2 μg/m3 of UFP in the mice model is equivalent to 7–86 μg/m3 in PM2.5 in mice and 29–86 μg/m3 in humans, which is a dose representative to a human exposure in a highly polluted city according to the World Health Organization -Exposure to ambient air pollution from particulate matter report [46] and based on the study of Gavett et al. [47].

The reduction of the dams’ weight at GD17.5 in the UFP exposed group could be due to a lesser physiological weight gain during pregnancy and the lower litter size (Additional file 1: Table S2). Also, promoted placental stress as manifested by decreased weight in the fetus at GD 17.5, an increased number of resorbed embryos, intrauterine inflammation and oxidative damage. The exposure also induced the HPA axis as indicated by increases in the cortisol levels in the dam and fetal sera, decreased dam weights and decreased protein levels and hypermethylation in two CpG sites of the promoter region of the HSD11B2. PND 50 male offspring demonstrated altered blood pressure, possibly triggered by RAS-related elements; we observed increased protein and hypomethylation levels in the promoter region of ACE and AT1R. These findings are consistent with the findings of Barker et al. [6], who described the link between intrauterine adversity by environmental stressors with an increased risk of CVD in adulthood.

In this study, we focused on the in utero exposure to UFP and observed a significant decrease in placenta and fetal weights at GD 17.5: low birth weight is one of the main effects observed from in utero PM exposure [48, 49] and has been used as a marker of an adverse intrauterine environment. Also, we observed that placental weight was also decreased as a result of the exposure to UFP. Although there are few experimental findings after PM exposure on the placenta and fetal weight, our findings are consistent with other published results. Exposure to diesel exhaust particles (DEP), resulted in a decreased placental weight in pregnant female C57Bl/6J mice exposed to 300 μg/m3 DEP [11], and in a reduction in the offspring body weight of C57BL/6BomTac after exposure of the pregnant mice to 19 mg/m3 DEP [50]. Low birth weight is also associated with an increased risk of subsequent adult diseases, including hypertension, and other cardiovascular diseases [51, 52]. Furthermore, we observed that placental weight was decreased by the in utero UFP exposure. Epidemiological evidence has shown that the weight and specific features of placental development are related to hypertension, the risk of cardiac death, and the estimated risk of death from coronary artery disease in the offspring in later life [53, 54]. The placenta is critical for normal fetal growth and development. However, a dysfunction in its homeostasis is responsible for triggering mechanisms related to CVD at adulthood [55, 56]. Here, we observed placental dysfunction due to the in utero exposure to UFP and possibly related to high cortisol levels which may have resulted from a decrease in the protein expression of HSD11B2. The placental enzyme HSD11B2 inactivates glucocorticoids and thus protects the developing fetus from the deleterious effects of excess glucocorticoids [21]. Due to the increase of HPA axis activity, which had the consequence of an increase in the dam’s serum cortisol, and a reduction of placental HSD11B2 protein expression after in utero UFP exposure, the fetal level of cortisol was also increased. Epidemiological studies have shown similar effects on the serum levels of cortisol due to the activation of the HPA axis after the exposure to PM2.5 [22]. Although corticosterone is considered to be the main glucocorticoid involved in the regulation of stress responses in rodents, several studies have shown increased cortisol levels in plasma and adrenal glands of mice following environmental stress [41, 42]. Moreover, animal studies have shown that prenatal glucocorticoid excess that resulted from maternal stress or due to exogenous administration to the mother or the fetus was associated with gene programming effects of the cardiovascular system [57, 58]. The mechanisms by which glucocorticoids mediate these effects are unclear but may include epigenetic modifications. Interestingly, our data indicated that the in utero exposure to UFP significantly increased the HSD11B2 promoter methylation, which resulted in the decrease of HSD11B2 protein levels and high cortisol levels in fetuses. The increased methylation of HSD11B2 promoter is consistent with a previous study in a human population that showed that exposure to PM10 during early pregnancy was associated with HSD11B2 placental DNA methylation [23] and other genes [59].

We collected UFP of air from Mexico City, and according to the physicochemical characteristics such as rounded shape, the proportion of the components (OC>EC>others> metals), and high potential redox activity, we propose that the UFP came from anthropogenic sources of fuel burning, in accordance with the predominant sources in the area (heavy traffic and industry). Moreover, oxidative stress and inflammation have been well confirmed to induce stress and may potentially be involved in the perturbation of pregnancy and developmental toxicity. In the lungs of dams that were exposed to UFP, a significant increase in the 8-OHdG levels was observed, as well as an increase in the protein levels of CYP1A1 and NQO1: these enzymes induce ROS through the biotransformation of PAH (which are present in the UFP). On the other hand, we demonstrated pulmonary inflammation by the increase of pro-inflammatory and anti-inflammatory cytokines and chemokines. The increase in ROS generation, which was probably the result of PAH biotransformation, could increase pro-inflammatory cytokines, potentially through the activation of nuclear factor kappa B (NF-kΒ). Consistently, animal studies have shown increased pulmonary inflammation after intratracheal instillation of ultrafine DEP [60, 61]. In addition, we observed systemic inflammation and a release of cytokines from the lung into the systemic circulation as demonstrated by increases in IL-1β and IL-6 in the dam sera. Inflammatory mediators derived from systemic circulation may be transported to the intrauterine environment, the dam’s essential organs and to fetal tissues, thus inducing placental stress. Several constituents of the particles, such as PAH and metals, when present in the bloodstream can be factors that cause the inflammatory process. Additionally, the observed HPA axis activation could be stimulated by pro-inflammatory cytokines, such as IL-1β, TNFα and IL-6, as reported by John & Buckingham [62]. The biotransformation of PAH in the placenta and fetus could affect the expression of immunoregulatory genes, which suggests that the chronic activation of the AhR would lead to elevated IL-6, as indicated by various studies that have shown cross-talk between AhR and NF-kB [63]. We confirmed an increase in oxidative damage and IL-6 production in the exposed fetuses from this study. Surprisingly, the levels of vascular endothelial growth factor (VEGF) in the fetuses were decreased, an event that has been associated with feto-placental vascular dysfunction [64]. VEGF is an endothelial cell-specific mitogen that promotes placental vascularization, studies have reported a decrease in VEGF during preeclampsia [65].

According to our findings, in utero UFP exposure induced oxidative damage and inflammation in the placentas and fetuses. However, contrary to our expectations, the pun model mice transplacentally exposed to UFP showed a no significant increment in the levels of DNA deletions in RPE. It is possible that the UFP dose (70 μg/kg/day) used in this study was not enough to induce detectable DNA deletions. Previous studies reporting the deletion of the pun gene after exposure to DEP and TiO2 nanoparticles during gestation used much higher doses (500 mg/kg/day) [16, 17].

Finally, we suggest that the suboptimal environment generated by the UFP exposure can affect the programming of CVD. Developmental programming, or developmental origins of health and disease, refers to the changes in fetal structure and physiology that result from adverse early life exposures that lead to increased disease risk in later life [66]. Programmed characteristics are believed to be largely stable after the postnatal period and have been associated with increased risk of coronary heart disease, type 2 diabetes, stroke and hypertension [6]. Stressors that lead to fetal programming have been identified and include nutritional factors such as over- and undernutrition [67], high glucocorticoid exposure and environmental pollutants [68]. However, results regarding the developmental origins of health and diseases (DOHaD) have been associated, later in life, with an increased risk of cardiovascular pathologies, such as hypertension [5]. In this regard, the RAS is strongly involved in blood pressure regulation and cardiovascular disease programming; hence, the overexpression of ACE and AT1R in the lung may induce hypertension. Our findings showed that in utero UFP exposure significantly decreased the %5-mC in the Ace, Agtr1a, and Agtr1a promoter regions in the fetuses and lungs of the male offspring at PND 50. The expression of the ACE and AT1R proteins in the fetuses and lungs of the male offspring correlated well with the DNA methylation levels. Methylation alterations in RAS-related genes, such as Ace, Agtr1a, and Agtr1b, have been shown to play a role in the fetal programming of hypertension [6971]. Hence, the increased blood pressure in the offspring at PND 50 was consistent with the over-expression of components of the RAS in the lung. Although AT1a is expressed in all tissues, AT1b is expressed only in the adrenal glands. A previous study by Goodson et al. [72] adds support to the finding that in utero exposure to PM promotes susceptibility to cardiovascular disease, inasmuch as they observed differential methylation of a gene identified as likely playing an important role in mediating adult sensitivity to heart failure (Mir133a-2) after in utero exposure to DEP.

Currently, the modulation of epigenetic biomarkers in utero is unclear, but it has been suggested that the presence of ROS can directly or indirectly affect DNA methylation, which results in persistent transcriptional changes [73]. In in vitro studies, 8-OHdG inhibits the methylation of the adjacent cytosines [74], a reaction that is catalyzed by DNA methyltransferases (DNMTs). Furthermore, 8-OHdG can influence the interaction of DNA with various transcription factors [75]. Although the mechanisms by which environmental stressors in utero alter the developing embryo and fetus are not clear. We suggest that the scenario caused by the in utero UFP exposure contributed to the fetal programming of RAS-related elements and altered blood pressure in the male offspring at adulthood. Recent studies on in utero exposure to particulate matter have shown oxidative stress, placental insufficiency [11], and cardiovascular susceptibility [10, 76], consistent with our findings. Furthermore, several experimental models of programming induced by gestational protein restriction [77, 78], maternal stress or placental insufficiency [79] have demonstrated that the induced hypertension is related to a marked increase in glucocorticoid expression and/or marked decrease in the expression of HSD11B2 [80].


Our data suggested that the in utero exposure to UFP influenced adult susceptibility to increased blood pressure, which was influenced by alterations in the placenta and hypomethylation of the promoter region of RAS-related elements. The present study provided evidence of the consequence of air pollution exposure during development and gestation, where in utero exposure to UFP influenced the susceptibility to CVD in adulthood. These effects should be addressed in polluted cities as a public health issue.



The authors would like to acknowledge the support of the Laboratorio Nacional de Nanoscopía Electrónica-Cinvestav-IPN.


This work was supported by Consejo Nacional de Ciencia y Tecnología (Conacyt)-México, Project number 167778 and 286739, and REDCAM.

Availability of data and materials

All data generated or analysed during this study are included in this published article [and its additional files].

Authors’ contributions

RAMR performed the animal exposure, characterized UFP, proposed the molecular targets, designed the primer sequences for methylation assessment, carried out the molecular biology, analyzed the data and wrote the manuscript. IAC helped in the primer sequences design for methylation assessment, and helped in the methylation assessment. NML helped in RPE determination technique, and in the animal mating and fetus tissue collection. TMUR helped in animal handling, obtaining samples and standardizing techniques. MAAO participated in UFP sample collection and the animal exposure. BQV revised the methylation data and advised in results interpretation. AOV revised the manuscript, discussed and analyzed the results. ADVR revised and developed the animal exposure, carried out its design and coordination, and supervised the draft of the manuscript. All authors read and approved the final manuscript.

Ethics approval

All animal procedures were approved by the Internal Committee for the Use and Care of Laboratory Animals, Cinvestav, in accordance to the “Principles of Laboratory Animal Care” guidelines under protocol No. 0171–15.

Consent for publication

Not applicable.

Competing interests

The authors declare that they have no competing interests.

Publisher’s Note

Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (, 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 ( applies to the data made available in this article, unless otherwise stated.

Authors’ Affiliations

Departamento de Toxicología, Centro de Investigación y de Estudios Avanzados del IPN, Ciudad de México, México
Departamento de Fisiología, Biofísica y Neurociencias, Centro de Investigación y de Estudios Avanzados del IPN, Ciudad de México, México
Departamento de Investigación Básica, Instituto Nacional de Cancerología, Ciudad de México, México
Department of Pediatrics, University of Alberta, Edmonton, Alberta, Canada


  1. Pope CA, Burnett RT, Thun MJ, Calle EE, Krewski D, Ito K, et al. Lung cancer, cardiopulmonary mortality, and long-term exposure to fine particulate air pollution. JAMA. 2002;287:1132–41.View ArticleGoogle Scholar
  2. Brook RD, Rajagopalan S, Pope CA, Brook JR, Bhatnagar A, Diez-Roux AV, Holguin F, Hong Y, Luepker RV, Mittleman MA, et al. Particulate matter air pollution and cardiovascular disease: an update to the scientific statement from the American heart association. Circulation. 2010;121:2331–78.View ArticleGoogle Scholar
  3. Brook RD, Urch B, Dvonch JT, et al. Insights into the mechanisms and mediators of the effects of air pollution exposure on blood pressure and vascular function in healthy humans. Hypertension. 2009;54(3):659–67.View ArticleGoogle Scholar
  4. Stone V, Miller MR, Clift MJD, Elder A, Mills NL, Møller P, et al. Nanomaterials versus ambient ultrafine particles: an opportunity to exchange toxicology knowledge. Environ Health Perspect. 2017;125(10):106002.View ArticleGoogle Scholar
  5. Kumar S, Verma MK, Srivastava AK. Ultrafine particles in urban ambient air and their health perspectives. Rev Environ Health. 2013;28:117–28.View ArticleGoogle Scholar
  6. Barker DJ, Eriksson JG, Forsén T, Osmond C. Fetal origins of adult disease: strength of effects and biological basis. Int J Epidemiol. 2002;31:1235–9.View ArticleGoogle Scholar
  7. Barker DJ, Osmond C. Low birth weight and hypertension. BMJ. 1988;297:134–5.View ArticleGoogle Scholar
  8. Klepac P, Locatelli I, Korošec S, Künzli N, Kukec A. Ambient air pollution and pregnancy outcomes: a comprehensive review and identification of environmental public health challenges. Environ Res. 2018;167:144–59.View ArticleGoogle Scholar
  9. Dissanayake HU, Skilton MR, Polson JW. Autonomic dysfunction in programmed hypertension. J Hum Hypertens. 2018.
  10. Gorr MW, Velten M, Nelin TD, Youtz DJ, Sun Q, Wold LE. Early life exposure to air pollution induces adult cardiac dysfunction. Am J Physiol Heart Circ Physiol. 2014;307(9):H1353–60.View ArticleGoogle Scholar
  11. Weldy CS, Liu Y, Liggitt HD, Chin MT. In utero exposure to diesel exhaust air pollution promotes adverse intrauterine conditions, resulting in weight gain, altered blood pressure, and increased susceptibility to heart failure in adult mice. PLoS One. 2014;9(2).Google Scholar
  12. Yamashita K, Yoshioka Y, Higashisaka K, Mimura K, Morishita Y, Nozaki M, et al. Silica and titanium dioxide nanoparticles cause pregnancy complications in mice. Nat Nanotechnol. 2011;6(5):321–8.View ArticleGoogle Scholar
  13. Tian X, Zhu M, Du L, Wang J, Fan Z, Liu J, et al. Intrauterine inflammation increases materno-fetal transfer of gold nanoparticles in a size-dependent manner in murine pregnancy. Small. 2013;9(14):2432–9.View ArticleGoogle Scholar
  14. Hougaard KS, Campagnolo L, Chavatte-Palmer P, Tarrade A, Rousseau-Ralliard D, Valentino S, et al. A perspective on the developmental toxicity of inhaled nanoparticles. Reprod Toxicol. 2015;56:118–40.View ArticleGoogle Scholar
  15. Brilliant M, Gondo Y, Eicher E. Direct molecular identification of the mouse pink-eyed unstable mutation by genome scanning. Science. 1991;252(5005):566–9.View ArticleGoogle Scholar
  16. Reliene R, Hlavacova A, Mahadevan B, Bairdb WM, Schiestl RH. Diesel exhaust particles cause increased levels of DNA deletions after transplacental exposure in mice. Mutat Res. 2005;570:245–52.View ArticleGoogle Scholar
  17. Trouiller B, Reliene R, Westbrook A, Solaimani P, Schiestl RH. Titanium Dioxide Nanoparticles Induce DNA Damage and Genetic Instability In vivo in Mice 2009;8784–8789.Google Scholar
  18. Schiestl RH, Aubrecht J, Yap WY, Kandikonda S, Sidhom S. Polychlorinated biphenyls and 2,3,7,8-tetrachlorodibenzo-p-dioxin induce intrachromosomal recombination in vitro and in vivo. Cancer Res. 1997;57:4378–83.PubMedGoogle Scholar
  19. Niu Y, Chen R, Xia Y, Cai J, Ying Z, Lin Z, et al. Fine particulate matter constituents and stress hormones in the hypothalamus–pituitary–adrenal axis. Environ Int. 2018;119:186–92.View ArticleGoogle Scholar
  20. Moisiadis VG, Matthews SG. Glucocorticoids and fetal programming part 1: outcomes. Nat Rev Endocrinol. 2014;10(7):391–402.View ArticleGoogle Scholar
  21. Mark PJ, Augustus S, Lewis JL, Hewitt DP, Waddell BJ. Changes in the placental glucocorticoid barrier during rat pregnancy: impact on placental corticosterone levels and regulation by progesterone. Biol Reprod. 2009;80(6):1209–15.View ArticleGoogle Scholar
  22. Cai J, Zhao Y, Liu P, Xia B, Zhu Q, Wang X, et al. Exposure to particulate air pollution during early pregnancy is associated with placental DNA methylation. Sci Total Environ. 2017;607–608:1103–8.View ArticleGoogle Scholar
  23. Suzuki S, Tsubochi H, Ishibashi H, Matsuda Y, Suzuki T, Krozowski ZS, et al. Inflammatory mediators down-regulate 11beta-hydroxysteroid dehydrogenase type 2 in a human lung epithelial cell line BEAS-2B and the rat lung. Tohoku J Exp Med. 2005;207:293–301.View ArticleGoogle Scholar
  24. Peña CJ, Monk C, Champagne FA. Epigenetic effects of prenatal stress on 11 b - hydroxysteroid dehydrogenase-2 in the placenta and fetal brain. PLoS. 2012;7:1–9.Google Scholar
  25. Auclair G, Weber M. Mechanisms of DNA methylation and demethylation in mammals. Biochimie. 2012;94(11):2202–11.View ArticleGoogle Scholar
  26. Lavoie JL, Sigmund CD. Minireview: overview of the renin-angiotensin system–an endocrine and paracrine system. Endocrinology. 2003;144(6):2179–83.View ArticleGoogle Scholar
  27. Llorens-Cortes C, Greenberg B, Huang H, et al. Tissular expression and regulation of type 1 angiotensin II receptor sub- types by quantitative reverse transcriptase-polymerase chain reaction analysis. Hypertension. 1994;24(5):538–48.View ArticleGoogle Scholar
  28. Pei F, Wang X, Yue R, et al. Differential expression and DNA methylation of angiotensin type 1A receptors in vascular tissues during genetic hypertension development. Mol Cell Biochem. 2015;402:1–8.View ArticleGoogle Scholar
  29. Riviere G, Lienhard D, Andrieu T, et al. Epigenetic regulation of somatic angiotensin-converting enzyme by DNA methylation and histone acetylation. Epigenetics. 2011;6(4):478–89.View ArticleGoogle Scholar
  30. Aztatzi-Aguilar OG, Uribe-Ramírez M, Arias-Montaño JA, Barbier O, De Vizcaya-Ruiz A. Acute and subchronic exposure to air particulate matter induces expression of angiotensin and bradykinin-related genes in the lungs and heart: Angiotensin-II type-I receptor as a molecular target of particulate matter exposure. Part Fibre Toxicol. 2015;12(1).Google Scholar
  31. Gunnison A, Chen LC. Effects of subchronic exposures to concentrated ambient particles in mice: VI. Gene expression in heart and lung tissue. Inhal Toxicol. 2005;17(4–5):225–33.View ArticleGoogle Scholar
  32. Kim S, Jaques PA, Chang M, Froines JR, Sioutas C. Versatile aerosol concentration enrichment system (VACES) for simultaneous in vivo and in vitro evaluation of toxic effects of ultrafine, fine and coarse ambient particles part I: development and laboratory characterization. Aerosol Science. 2001;32(11):1281–97.View ArticleGoogle Scholar
  33. De Vizcaya-Ruiz A, Gutiérrez-Castillo ME, Uribe-Ramirez M, Cebrián ME, Mugica-Alvarez V, Sepúlveda J, et al. Characterization and in vitro biological effects of concentrated particulate matter from Mexico City. Atmos Environ. 2006;40:583–92.View ArticleGoogle Scholar
  34. Amador-Muñoz O, Bazán-Torija S, Villa-Ferreira SA, Villalobos-Pietrini R, Bravo-Cabrera JL, Munive-Colín Z, et al. Opposing seasonal trends for polycyclic aromatic hydrocarbons and PM10: health risk and sources in Southwest Mexico City. Atmos Res. 2013;122:199–212.View ArticleGoogle Scholar
  35. Cho AK, Sioutas C, Miguel AH, Kumagai Y, Schmitz DA, Singh M, Eiguren-Fernandez A, Froines JR. Redox activity of airborne particulate matter at different sites in the Los Angeles Basin. Environ Res. 2005;99:40–7.View ArticleGoogle Scholar
  36. Byers SL, Wiles MV, Dunn SL, Taft RA. Mouse estrous cycle identification tool and images. PLoS One. 2012;7:2–6.View ArticleGoogle Scholar
  37. Heyne GW, Plisch EH, Melberg CG, Sandgren EP, Peter JA, Lipinski RJ. A simple and reliable method for early pregnancy detection in inbred mice. J Am Assoc Lab Anim Sci JAALAS. 2015;54:368–71.PubMedGoogle Scholar
  38. Jackson P, Lund SP, Kristiansen G, Andersen O, Vogel U, Wallin H, et al. An experimental protocol for maternal pulmonary exposure in developmental toxicology. Basic Clin Pharmacol Toxicol. 2010;108(3):202–7.View ArticleGoogle Scholar
  39. Gondo Y, Gardner JM, Nakatsu Y, Durham-pierre D, Deveaut SA, Kuper C, et al. High-frequency genetic reversion mediated by a DNA duplication: the mouse pink-eyed unstable mutation. Proc Natl Acad Sci U S A. 1993;90:297–301.View ArticleGoogle Scholar
  40. Cain DW, Cidlowski JA. Specificity and sensitivity of glucocorticoid signaling in health and disease. Best Pract Res Clin Endocrinol Metab. 2015;29:545–56.View ArticleGoogle Scholar
  41. Nakamura K, Aoike A, Hosokawa T, Rokutan K, Koyama K, et al. Effect of food-restriction stress on immune response in mice. J Neuroimmunol. 1990;30(1):23–9.View ArticleGoogle Scholar
  42. Won SJ, Lin MT. Thermal stresses reduce natural killer cell cytotoxicity. J Appl Physiol. 1985;79:732–7.View ArticleGoogle Scholar
  43. Li L-C, Dahiya R. MethPrimer: designing primers for methylation PCRs. Bioinformatics. 2002;18(11):1427–31.View ArticleGoogle Scholar
  44. University of California Santa Cruz. UCSC Genome Browser. Accessed Oct 2017.
  45. Kitami Y, Okura T, Marumoto K, et al. Differential gene expression and regulation of type-1 angiotensin II receptor subtypes in the rat. Biochem Biophys Res Commun. 1992;188(1):446–52.View ArticleGoogle Scholar
  46. World Health Organization. Exposure to ambient air pollution from particulate matter for 2016 (
  47. Gavett SH, Haykal-Coates N, Highfill JW, Ledbetter AD, Chen LC, Cohen MD, et al. World trade center fine particulate matter causes respiratory tract hyperresponsiveness in mice. Environ Health Perspect. 2003;111(7):981–91.View ArticleGoogle Scholar
  48. Dadvand P, Parker J, Bell ML, Bonzini M, Brauer M, Darrow LA, Gehring U, Glinianaia SV, Gouveia N, Ha E-H, et al. Maternal exposure to particulate air pollution and term birth weight: a multi-country evaluation of effect and heterogeneity. Environ Health Perspect. 2013;121:267–373.View ArticleGoogle Scholar
  49. Lee BE, Ha EH, Park HS, Kim YJ, Hong YC, Kim H, Lee JT. Exposure to air pollution during different gestational phases contributes to risks of low birth weight. Hum Reprod. 2003;18:638–43.View ArticleGoogle Scholar
  50. Hougaard KS, Jensen KA, Nordly P, Taxvig C, Vogel U, Saber AT, Wallin H. Effects of prenatal exposure to diesel exhaust particles on postnatal development, behavior, genotoxicity and inflammation in mice. Particle and Fibre Toxicology. 2008;5(3):1–15.Google Scholar
  51. Xu XF, Du LZ. Epigenetics in neonatal diseases. Chin Med J. 2010;123:2948–54.PubMedGoogle Scholar
  52. Crispi F, Miranda J, Gratacós E. Long-term cardiovascular consequences of fetal growth restriction: biology, clinical implications, and opportunities for prevention of adult disease. Am J Obstet Gynecol. 2018;218:S869–79.View ArticleGoogle Scholar
  53. Godfrey KM. The role of the placenta in fetal programming – a review. Placenta. 2002;23(Suppl. A):S20–7.View ArticleGoogle Scholar
  54. Risnes KR, Romundstad PR, Nilsen TI, Eskild A, Vatten LJ. Placental weight relative to birth weight and long-term cardiovascular mortality: findings from a cohort of 31,307 men and women. Am J Epidemiol. 2009;170(5):622–31.View ArticleGoogle Scholar
  55. Barker DJ, Thornburg KL, Osmond C, Kajantie E, Eriksson JG. The surface area of the placenta and hypertension in the offspring in later life. Int J Dev Biol. 2010;54(2–3):525–30.View ArticleGoogle Scholar
  56. Bronson SL, Bale TL. The placenta as a mediator of stress effects on neurodevelopmental reprogramming. Neuropsychopharmacology. 2016:207–18.Google Scholar
  57. Igosheva N, Klimova O, Anishchenko T, Glover V. Prenatal stress alters cardiovascular responses in adult rats. J Physiol. 2004;557:273–85.View ArticleGoogle Scholar
  58. Forhead AJ, Jellyman JK, De Blasio MJ, Johnson E, Giussani DA, Pipkin FB, et al. Maternal dexamethasone treatment alters tissue and circulating components of the renin-angiotensin system in the pregnant ewe and fetus. Endocrinology. 2015;156:3038–46.View ArticleGoogle Scholar
  59. Abraham E, Rousseaux S, Agier L, Giorgis-Allemand L, Tost J, Galineau J, et al. Pregnancy exposure to atmospheric pollution and meteorological conditions and placental DNA methylation. Environ Int. 2018;118:334–47.View ArticleGoogle Scholar
  60. Miyabara Y, Yanagisawa R, Shimojo N, Takano H, Lim HB, Ichinose T, et al. Murine strain differences in airway inflammation caused by diesel exhaust particles. Eur Respir J. 1998;11(2):291–8.View ArticleGoogle Scholar
  61. Evans SA, Al-Mosawi A, Adams RA, Bérubé KA. Inflammation, edema, and peripheral blood changes in lung-compromised rats after instillation with combustion-derived and manufactured nanoparticles. Exp Lung Res. 2006;32(8):363–78.View ArticleGoogle Scholar
  62. John CD, Buckingham JC. Cytokines: regulation of the hypothalamo-pituitary-adrenocortical axis. Curr Opin Pharmacol. 2003;3(1):78–84.View ArticleGoogle Scholar
  63. Vogel CFA, Matsumura F. A new cross-talk between the aryl hydrocarbon receptor and RelB, a member of the NF-κB family. Biochem Pharmacol. 2009;77(4):734–45.View ArticleGoogle Scholar
  64. Nadar SK, Karalis I, Al Yemeni E, Blann AD, Lip GY. Plasma markers of angiogenesis in pregnancy induced hypertension. Thromb Haemost. 2005;94:1071–6.View ArticleGoogle Scholar
  65. Lyall F, Young A, Boswell F, Kingdom JC, Greer IA. Placental expression of vascular endothelial growth factor in placentae from pregnancies complicated by pre-eclampsia and intrauterine growth restriction does not support placental hypoxia at delivery. Placenta. 1997;18:269–76.View ArticleGoogle Scholar
  66. Thornburg KL, et al. In utero life and epigenetic predisposition for disease. Adv Genet. 2010;71:57–78.View ArticleGoogle Scholar
  67. Burdge G, Lillycrop K. Nutrition, epigenetics, and developmental plasticity: implications for understanding human disease. Annu Rev Nutr. 2010;30:315–39.View ArticleGoogle Scholar
  68. Wright R, Brunst K. Programming of respiratory health in child- hood: influence of outdoor air pollution. Curr Opin Pediatr. 2013;25(2):232–9.View ArticleGoogle Scholar
  69. Moritz KM, Cuffe JS, Wilson LB, Dickinson H, Wlodek ME, Simmons DG, Denton KM. Review: sex specific programming: a critical role for the renal renin-angiotensin system. Placenta. 2010;31:S40–6.View ArticleGoogle Scholar
  70. Vieira-Rocha MS, Rodríguez-Rodríguez P, Sousa JB, González MC, Arribas SM, López de Pablo AL, et al. Vascular angiotensin AT1 receptor neuromodulation in fetal programming of hypertension. Vasc Pharmacol. 2018;1891(18):30246–5.Google Scholar
  71. Bogdarina I, Welham S, King PJ, et al. Epigenetic modification of the renin- angiotensin system in the fetal programming of hypertension. Circ Res. 2007;100(4):520–6.View ArticleGoogle Scholar
  72. Goodson JM, Weldy CS, MacDonald JW, Liu Y, Bammler TK, Chien WM, et al. In utero exposure to diesel exhaust particulates is associated with an altered cardiac transcriptional response to transverse aortic constriction and altered DNA methylation. FASEB J. 2017;31:4935–45.View ArticleGoogle Scholar
  73. Rodríguez-Rodríguez P, Ramiro-Cortijo D, Reyes-Hernández CG, López de Pablo AL, Carmen González M, Arribas SM. Implication of oxidative stress in fetal programming of cardiovascular disease. Front Physiol. 2018;23(9):602.View ArticleGoogle Scholar
  74. Maltseva DV, Baykov AA, Jeltsch A, et al. Impact of 7,8-dihydro-8-oxoguanine on methylation of the CpG site by Dnmt3a. Biochemistry. 2009;48:1361–8.View ArticleGoogle Scholar
  75. Ghosh R, Mitchell DL. Effect of oxidative DNA damage in promoter elements on transcription factor binding. Nucleic Acids Res. 1999;27:3213–8.View ArticleGoogle Scholar
  76. Weldy CS, Liu Y, Chang YC, Medvedev IO, Fox JR, Larson TV, et al. In utero and early life exposure to diesel exhaust air pollution increases adult susceptibility to heart failure in mice. Part Fibre Toxicol. 2013;10(1):59.View ArticleGoogle Scholar
  77. Langley-Evans SC, Phillips GJ, Benediktsson R, Gardner DS, Edwards CR, Jackson AA, Seckl JR. Protein intake in pregnancy, placental glucocorticoid metabolism and the programming of hypertension in the rat. Placenta. 1996;17(2–3):169–72.View ArticleGoogle Scholar
  78. Bertram C, Trowern AR, Copin N, Jackson AA, Whorwood CB. The maternal diet during pregnancy programs altered expression of the glucocorticoid receptor and type 2 11beta-hydroxysteroid dehydrogenase: potential molecular mechanisms underlying the programming of hypertension in utero. Endocrinology. 2001;142(7):2841–53.View ArticleGoogle Scholar
  79. Baserga M, Kaur R, Hale MA, Bares A, Yu X, et al. Fetal growth restriction alters transcription factor binding and epigenetic mechanisms of renal 11beta-hydroxysteroid dehydrogenase type 2 in a sex-specific manner. Am J Physiol Regul Integr Comp Physiol. 2010;299:R334–42.View ArticleGoogle Scholar
  80. Perrone S, Santacroce A, Picardi A, Buonocore G. Fetal programming and early identification of newborns at high risk of free radical-mediated diseases. World J Clin Pediatr. 2016;5(2):172–81.View ArticleGoogle Scholar


© The Author(s). 2019


By submitting a comment you agree to abide by our Terms and Community Guidelines. If you find something abusive or that does not comply with our terms or guidelines please flag it as inappropriate. Please note that comments may be removed without notice if they are flagged by another user or do not comply with our community guidelines.