Review of epidemiological studies on air pollution and health effects in children

Jong-Tae Lee

doi:10.3345/cep.2019.00843

Clin Exp Pediatr > Volume 64(1); 2021

Lee: Review of epidemiological studies on air pollution and health effects in children

Review Article

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Review of epidemiological studies on air pollution and health effects in children

Jong-Tae Lee, PhD

Division of Health Policy and Management, College of Health Science, Korea University, Seoul, Korea

Corresponding author: Jong-Tae Lee, PhD. School of Health Policy and Management, College of Health Science, Korea University, 145 Anam-ro, Seongbuk-gu, Seoul 02841, Korea E-mail: jtlee@korea.ac.kr

Received July 17, 2019 Revised January 21, 2020 Accepted February 28, 2020

This is an Open Access article distributed under the terms of the Creative Commons Attribution Non-Commercial License (http://creativecommons.org/licenses/by-nc/4.0/) which permits unrestricted non-commercial use, distribution, and reproduction in any medium, provided the original work is properly cited.

Clinical and Experimental Pediatrics 2021;64(1):3-11.

Published online: June 10, 2020

DOI: https://doi.org/10.3345/cep.2019.00843

Abstract

There is a growing body of literature on the adverse health effects of ambient air pollution. Children are more adversely affected by air pollution due to their biological susceptibility and exposure patterns. This review summarized the accumulated epidemiologic evidence with emphasis on studies conducted in Korea and heterogeneity in the literature. Based on systematic reviews and meta-analyses, there is consistent evidence on the association between exposure to ambient air pollution and children’s health, especially respiratory health and adverse birth outcomes, and growing evidence on neurodevelopmental outcomes. Despite these existing studies, the mechanism of the adverse health effects of air pollution and the critical window of susceptibility remain unclear. There is also a need to identify causes of heterogeneity between studies in terms of measurement of exposure/outcome, study design, and the differential characteristics of air pollutants and population.

Key words: Air pollution, Children, Respiratory health, Birth outcomes, Infant mortality, Neurodevelopment

Key message

This review summarized the accumulated epidemiologic evidence with emphasis on studies conducted in Korea and heterogeneity in the literature. Based on systematic reviews and meta-analyses, there is consistent evidence on the association between exposure to ambient air pollution and children’s health, especially respiratory health and adverse birth outcomes, and growing evidence on neurodevelopmental outcomes.

Introduction

There is a growing body of literature on the adverse health effects of ambient air pollution [1-3]. Epidemiological studies to date have consistently reported that chronic and acute exposure to ambient air pollutants is related to an increased risk of cardiopulmonary health. Some of these studies focused on a susceptible population at higher risk posed by air pollution, which raised concerns regarding child susceptibility. Children are more adversely affected by air pollution due to their immature immune systems, their underdeveloped lung and metabolic systems, and the co-occurrence of infection with respiratory pathogens [4,5]. Children are also susceptible to air pollution because they spend more time outdoors and are more physically active, which results in exposure to a higher concentration of air pollution and increased ventilation rates [6].

Numerous systematic reviews and meta-analyses have examined air pollution and children’s health, including the World Health Organization (WHO) reports published in 2005 and 2018 [5,7]. This review is in line with previous studies that summarized and evaluated the accumulated epidemiologic evidence but puts more emphasis on studies conducted in South Korea and discusses the causes of heterogeneity in the literature. In this context, we limited the scope of this review to ambient air pollution and the most commonly investigated health outcomes.

Respiratory health

Since air pollution enters the human body through breathing, the respiratory system is primarily and directly exposed to air pollution. Numerous epidemiologic studies have investigated the respiratory effects of air pollution on children, including lung function and respiratory symptoms/diseases. The systematic reviews and meta-analyses on ambient air pollution and children’s respiratory health examined here are shown in Table 1 [8-21].

Meta-analyses concluded that air pollution may adversely impact lung function. However, Ward and Ayres [8] suggested that the reliability of summary effect estimates is limited due to considerable heterogeneity and possible publication bias. They highlighted the need for further research on the causes of this heterogeneity, including an analytic approach, study population, and interactions between air pollutants. Studies on the Korean population have consistently suggested adverse effects of airborne particles on lung function [22-24]; however, making a direct comparison of the effect estimates between these studies was difficult since they used different study designs.

As concluded by the WHO report [5], the results of metaanalyses on asthma incidence and prevalence were inconsistent in terms of outcomes and individual pollutants. Anderson and colleagues conducted two meta-analyses on asthma incidence and prevalence and found that only NO₂ was associated with the incidence of asthma [9,10]. In Korea, a prospective study of elementary school children showed that ambient O₃ was positively associated with the 1-year prevalence of wheezing (odds ratio [OR], 1.372; 95% confidence interval [CI], 1.016–1.852; per 5 ppb) [25]. However, Yi et al. [26] did not find a significant association between traffic-related air pollution (TRAP) exposure and asthma prevalence in Seoul, Korea.

Emergency departments and hospital admissions for asthma have been used in many studies as a surrogate for asthma exacerbation. Several meta-analyses have consistently reported significant effects of air pollution on the increase in hospital utilization for asthma [11-14]. Fan et al. [11] and Zhang et al. [14] showed that the magnitude of the association between hospital utilization for asthma and exposure to air pollution was larger in children than in adults. Previous studies conducted in Korea also provided convincing evidence of the positive association of air pollutants with hospital admissions for asthma [27-32].

Studies on asthma incidence and prevalence varied in terms of exposure assessment methods, and outcome measurements were often made via questionnaire. The studies had different designs: cohort, case-control, and cross-sectional. On the other hand, every study on asthma exacerbation used hospital records to define health outcomes. They also used time-series analyses or case-crossover designs in common to evaluate the short-term effect. These differences may be the reason why evidence of the link between air pollution and asthma exacerbation is robust, while studies on asthma incidence and prevalence reported relatively large degrees of heterogeneity and inconsistent results.

One of the diseases mainly studied in relation to respiratory health is respiratory infections, including pneumonia. In a meta-analysis, Mehta et al. [15] showed that long-term ambient particulate matter (PM_2.5) exposure was associated with an increased risk of acute lower respiratory infections. Short-term exposure to air pollution has also been reported to be associated with increased hospital admission or health care utilization for respiratory infections [33,34].

These respiratory health effects of air pollution can lead to school absenteeism for children. A study from Mexico City revealed that a high concentration of ambient ozone for 2 consecutive days increased the risk of school absenteeism for respiratory illness by about 20% [35]. Park et al. [36] showed that PM₁₀, O₃, and SO₂ were associated with illness-related absenteeism in elementary school students in South Korea. However, the study of a cohort in southern California communities did not find a statistically significant association between school absenteeism and PM₁₀ or NO₂ [37]. Although studies on school absenteeism are limited in terms of outcome measure, these kinds of studies support the evidence that air pollution affects the respiratory health of children.

Several recent studies suggested seasonal variations in the association between air pollution and respiratory health in children. Stronger effects of air pollution were found during the cold season [34,38] or transient season [39]. These various effects of season might have been induced by a different meteorological condition affecting the distribution of air pollution or different outdoor behaviors of children affecting exposure pattern. Children’s respiratory health can also be affected by seasonal factors such as viral infections or allergens. Therefore, studies of air pollution and respiratory health for children must consider season as an important factor.

Adverse birth outcomes and early childhood mortality

Adverse birth outcomes are a matter of great concern because their effects influence health throughout life [40-42]. There is growing evidence of the associations between maternal exposure to ambient air pollution and adverse birth outcomes, including low birth weight (LBW), preterm birth (PTB), stillbirth (SB), and small for gestational age (SGA). The systematic reviews and meta-analyses considered here are shown in Table 2 [43-50]. Overall, there is compelling evidence that exposure to ambient air pollution, mainly PM, NO₂, SO₂, and CO, is associated with LBW, SGA, and PTB, but there is mixed evidence regarding its contributions to SB. Studies conducted in Korea also provided a consistent conclusion regarding the association between air pollution and LBW [51-53], PTB [54,55], and SB [56].

Recent studies have focused on the heterogeneity of the effects of air pollutants on adverse birth outcomes. Several studies investigated the effects of PM according to its chemical constituents to identify major contributors with detrimental health effects [57-59]. For example, a recent meta-analysis by Sun et al. [60] reported that zinc, nickel, titanium, vanadium, organic carbon, nitrate, and elemental carbon were associated with LBW. Other studies focused on population characteristics as causes of heterogeneity, such as a child’s sex [61] and maternal socioeconomic status [62]. Recent studies also considered area-level characteristics such as residential socioeconomic status [63,64] or greenness level. [65] For example, Yi et al. [66] reported that the effect of PM₁₀ on PTB was stronger among mothers living in deprived areas after the adjustment for individual-level socioeconomic status in Seoul, Korea.

The results of previous studies regarding the critical exposure period vary according to the study population, location, and air pollutants. A recent meta-analysis showed that the association was the strongest for PM_2.5 exposure in late pregnancy with LBW infants [60]. Another meta-analysis reported the highest pooled estimates for PM₁₀ exposure in the first trimester with LBW or PTB but no notable differences for NO₂ across pregnancy trimesters [43]. Studies in Korea reported the strongest associations between exposure to air pollutants in early to midpregnancy and LBW [51,52], while others reported the strongest associations between exposure to air pollution in the third trimester and PTB [54,67]. Several plausible mechanisms support early or late pregnancy as a critical period [60,68-70], but more evidence is needed to clarify the critical window of susceptibility and its biological mechanisms.

There is also strong evidence that exposure to ambient air pollution is associated with infant mortality, particularly respiratory deaths and sudden infant death syndrome (SIDS) [71-73]. In Korea, Ha et al. [74] and Hwang et al. [75] reported on the effects of acute exposure to PM₁₀ on cause-specific mortality and SIDS, respectively. Most studies to date focused on short-term exposure to air pollution, and few have provided evidence of the effects of long-term exposure. For example, Son et al. [76] reported the association between long-term exposure to PM (total suspended particles, PM₁₀, PM_10-2.5, PM_2.5) and infant mortality in Seoul, Korea.

Neurodevelopmental outcomes

Neurodevelopment is an emerging research area in air pollution and children’s health. Although evidence is still mounting, existing studies have suggested the potential associations between prenatal/postnatal exposure to ambient air pollution and neurodevelopmental effects such as cognitive development, autism spectrum disorder (ASD), and attention-deficit hyperactivity disorder (ADHD). A summary of individual studies and meta-analyses is provided in Table 3 [77-88]. There is growing evidence that exposure to air pollution, particularly TRAP, is related to cognitive and psychomotor development in children [89,90]. Several studies reported that pre- and postnatal exposure to polycyclic aromatic hydrocarbons (PAHs) [77-80,91], PM_2.5, and NO₂ [81,82] adversely affected cognitive development and behavior. Kim et al. [83] investigated the adverse effects of prenatal exposure to PM₁₀ and NO₂ on neurodevelopment over 24 months in Korean children. They found significant associations between PM₁₀ and both cognitive and psychomotor development. Prenatal exposure to NO₂ also adversely affected psychomotor but not cognitive development.

It is also noteworthy to highlight the association between air pollution and neurodevelopment disorders. A recent meta-analysis reported positive associations between prenatal exposures to PM₁₀, PM_2.5, NO₂, and O₃ with ASD. Postnatal exposure to PM_2.5 and NO₂ was associated with ASD. Relatively few studies investigated the associations between air pollution and ADHD; thus, those results are not yet conclusive. Newman et al. [84] found that exposure to elemental carbon attributed to traffic during the first year of life was related to higher scores of ADHD-related symptoms in children. Meanwhile, Forns et al. [85] examined the associations between exposure to TRAP, including elemental carbon, black carbon, and NO₂, at school and ADHD-DSM-IV scores and found no significant associations with ADHD symptoms. In Korea, Min and Min [86] reported a significant association between exposure to PM₁₀ and NO₂ with childhood ADHD incidence, but further studies of different populations, the time window of exposure, and confounding are needed.

Overall, there is relatively consistent evidence of the associations between ambient air pollution and neurodevelopmental effects. However, there is a need to clarify the critical window of exposure in the pre- and postnatal periods. Moreover, further research must compare studies using different exposure/outcome measurements and investigate the effects of sex, age, and environmental and social conditions.

Discussion

Most studies investigating the health effects of ambient air pollution in children estimated the associations between individual air pollutants and specific health outcomes. One of the common limitations of these studies is that it is difficult to assess the effects of exposure to multiple pollutants simultaneously. In the real world, the population is exposed to a mixture of pollutants in the atmosphere, so the health effects of air pollution may have been caused by a combination of those various pollutants. However, as air pollutants are correlated and interact with each other, it remains a challenge to disentangle the independent effects of individual pollutants or comprehensively estimate the effects of mixed air pollution.

The mechanisms of the adverse health effects of air pollution on children are also complex and remain unclear. Nonetheless, the inflammatory response and oxidative stress are often suggested to play important roles. In a panel study of New York City schoolchildren, Patel et al. [92] reported that black carbo and NO₂ were associated with pH and 8-isoprostane, exhaled biomarkers of airway inflammation and oxidative stress, respectively. Toxicological studies have suggested that PM may stimulate the formation of reactive oxygen species (ROS), and continuous ROS exposure can impair lung function through pulmonary inflammation [93]. It was recently suggested that epigenetic changes may be involved in mechanisms linking air pollution to health. Air toxicants may alter the methylation degree of candidate genes related to cardiovascular diseases, respiratory diseases, and cancer [94,95]. These epigenetic modifications are expected to help identify the causal correlation between air pollution exposure and children’s health.

Although the adverse effects of air pollution on health outcomes of children reviewed in this paper are generally well founded, different effect estimates or inconsistent results are often reported. There may be various reasons for heterogeneity between studies apart from analytical approaches, including study design and statistical methods. As mentioned before, air pollution is a mixture of various substances and individual air pollutants can interact with other air pollutants. The effects of individual pollutants can vary due to the different distribution of air pollutants between study areas. In particular, PM is a mixture of chemicals, unlike other gaseous pollutants. Since the toxicity of PM depends on chemical size and constituents [58,60,96,97], differences in PM characteristics between regions can be a major cause of heterogeneity among studies.

In addition to the properties of air pollution, population vulnerability can explain interstudy heterogeneity. Several studies have shown that individual sociodemographic characteristics or the local environment could modify the association between ambient air pollution and health [38,62,66]. Among various factors, age is one of the most important effect modifiers in the pediatric population. A child is usually defined as a person below the age of 18, but each study sets its own standard age. Even among populations under the age of 18, younger and older children may have different biological characteristics and outdoor activity patterns, resulting in inconsistent results between studies.

Accordingly, comparing existing studies requires an in-depth understanding of the characteristics of the study area and population. Related research has recently been underway in the Asian region and developing countries beyond the US and Europe. When researchers aggregate studies conducted in various regions, it will be important to explore how various heterogeneity factors can affect the study results. These efforts will help us understand the complex causal correlation between air pollution and children’s health, find gaps in existing research, and evolve to advanced research.

Epidemiological research on the health effects of air pollution provides scientific evidence for environmental health policy development. Environmental health policies should not only protect everyone’s health from air pollution, they should reduce the health inequality caused by air pollution. In terms of health inequality, it is essential to consider social determinants of health in relation to air pollution [98,99] because they can affect the level of exposure to air pollution and the vulnerability to air pollution. A Korean study showed that socioeconomic status measured at the individual and regional levels was correlated with air quality index [100]. Low socioeconomic status can also make individuals more vulnerable to air pollution exposure by limiting healthy behaviors or health care utilization. Therefore, future research on air pollution and children’s health should move toward considering various social contexts so that we can identify intervention points for reducing health inequality.

Conclusions

Review of the existing systematic reviews, meta-analyses, and recently updated studies revealed consistent evidence of the association between exposure to ambient air pollution and children’s health, especially respiratory health and adverse birth outcomes, and growing evidence on neurodevelopmental outcomes. Studies conducted in Korea also provided a consistent conclusion, although the number of studies remains limited.

Despite these existing studies, the mechanism of adverse health effects of air pollution and the critical window of susceptibility remain unclear. There is also a need to identify causes of heterogeneity between studies in terms of measuring exposure/outcome, study design, and differential characteristics of air pollutants and population.

Conflicts of interest

No potential conflict of interest relevant to this article was reported.

Table 1.

Summary of existing meta-analyses of correlation between air pollution and children’s respiratory health

Study	Pollutant	Exposure period	Outcome	No. of articles^a)	Main result
Barone-Adesi et al., 2015 [16]	NO₂	Long-term	Lung function (FEV₁)	13	Increase in NO₂ was associated with lower FEV₁ (absolute difference -8 mL; 95% CI, -14 to -1 mL per 10 μg/m³)
Ward & Ayres, 2004 [8]	PM₁₀, PM_2.5	Short-term	Lung function and respiratory symptoms (PEF, cough, LRS or wheeze)	22	Increase in PM₁₀ and PM_2.5 were associated with lower PEF and increasing risk of symptoms. Effects of PM₁₀ were widely spread and smaller than those for PM_2.5 (change in PEF PM_2.5: -0.063 L/min, 95% CI, -0.091 to 0.034 L/min; PM₁₀: -0.012 L/min, 95% CI, -0.017 to 0.008 L/min per 1 μg/m³)
Weinmayr et al., 2010 [17]	PM₁₀, NO₂	Short-term	Lung function and respiratory symptoms (PEF, cough, LRS or wheeze)	36	Increase in PM₁₀ was associated with increasing risk of asthma symptoms (OR 1.028; 95% CI, 1.006 to 1.051 per 10 μg/m³). The associations of PM₁₀ with cough and PEF were not statistically significant. The results for NO₂ depended on the lag times examined.
Bowatte et al., 2015 [18]	TRAP: NO₂, PM_2.5, BC	Long-term	Asthma (incidence)	19	Increase in PM_2.5 and BC were associated with increasing risk of asthma (PM_2.5: OR, 1.14, 95% CI, 1.00 to 1.30 per 2 μg/m³; BC: OR, 1.20, 95% CI, 1.05 to 1.38 per 1x10^-5m^-1)
Gasana et al., 2012 [19]	Motor vehicle air pollution: NO, NO₂, NOx, CO, PM_2.5, PM₁₀, SO₂, O₃	Long-term	Asthma, wheeze (incidence, prevalence)	19	Increase in NO₂, NO, CO, PM, and SO₂ were associated with increasing risk of asthma and/or wheeze (asthma prevalence NO₂: OR, 1.05, 95% CI, 1.00 to 1.11; NO: OR, 1.02, 95% CI, 1.00 to 1.04; CO: OR, 1.06, 95% CI, 1.01 to 1.12; wheeze pre-valence SO₂: OR, 1.04, 95% CI, 1.01 to 1.07; asthma incidence NO₂: OR, 1.14, 95% CI, 1.06 to 1.24; wheeze incidence PM: OR, 1.05, 95% CI, 1.04 to 1.07 per 10 μg/m³)
Khreis et al., 2017 [20]	TRAP: BC, NO₂, NOx, PM_2.5, PM₁₀	Long-term	Asthma (incidence, lifetime prevalence)	21	With the exception of NOx, increase in all pollutants were associated with increasing risk of asthma (BC: OR, 1.08, 95% CI, 1.03 to 1.14 per 0.5×10^-5m^-1; NO₂: OR, 1.05, 95% CI, 1.02 to 1.07 per 4 μg/m³; NOx: OR, 1.48, 95% CI, 0.89 to 2.45 per 30 μg/m³; PM_2.5: OR, 1.03, 95% C,I 1.01 to 1.05 per 1 μg/m³; PM₁₀: OR, 1.05, 95% CI, 1.02 to 1.08 per 2 μg/m³)
Anderson et al., 2013 [9]	PM₁₀, NO₂	Long-term	Asthma, wheeze (incidence, lifetime prevalence)	10	Increase in NO₂ was associated with increasing risk of asthma or wheeze (OR, 1.05; 95% CI, 1.01 to 1.10 per 10 μg/m³). The effect of PM₁₀ was not statistically significant.
Anderson et al., 2013 [10]	PM₁₀, NO₂, O₃, SO₂	Long-term	Asthma, wheeze (pre-valence)	8	All pollutants were not associated with prevalence or asthma or wheeze
Lim et al., 2016 [12]	PM_2.5	Short-term	Hospital admissions and emergency department visits for asthma	26	Increase in PM_2.5 was associated with hospital admissions and emergency department visits for asthma (RR, 1.048; 95% CI, 1.028 to 1.067 per 10 μg/m³)
Fan et al., 2016 [11]	PM_2.5	Short-term	Emergency department visits for pneumonia	16	Increase in PM_2.5 was associated with emergency department visits for asthma (RR, 1.036; 95% CI, 1.018 to 1.053 per 10 μg/m³)
Orellano et al., 2017 [13]	NO₂, SO₂, PM₁₀, PM_2.5, CO, O₃	Short-term	Hospital admissions and emergency department visits for asthma	16	Increase in NO₂, SO₂ and PM_2.5 were associated with asthma exacerbations (NO₂: OR, 1.040, 95% CI, 1.001 to 1.081 per 10 ppb; SO₂: OR, 1.047, 95% CI, 1.009 to 1.086 per 10 ppb; PM_2.5: OR, 1.022, 95% CI, 1.000 to 1.045 10 μg/m³)
Zhang et al., 2016 [14]	SO₂, NO₂, CO, O₃, PM₁₀	Short-term	Hospital utilization for asthma	26	All pollutants were associated with all-type hospital utilization for asthma (SO₂: RR, 1.057, 95% CI, 1.008 to 1.108 per 10 μg/m³; NO₂: RR, 1.035, 95% CI, 1.025 to 1.046 per 10 μg/m³; CO: RR, 1.141, 95% CI, 1.093 to 1.191 per 1 mg/m³; O₃: RR, 1.029, 95% CI, 1.022 to 1.037 per 10 μg/m³; PM₁₀: RR, 1.021, 95% CI, 1.017 to 1.024 10 μg/m³; PM_2.5: RR, 1.022, 95% CI, 1.019 to 1.026 10 μg/m³)
Mehta et al., 2013 [15]	PM_2.5	Long-term	Acute lower respiratory infections (ALRI)	4	Increase in PM_2.5 was associated with increasing risk of ALRI (RR, 1.12; 95% CI, 1.03 to 1.30 per 10 μg/m³)
Nhung et al., 2017 [21]	PM₁₀, PM_2.5, SO₂, O₃, NO₂, CO	Short-term	Hospital admissions and emergency department visits for pneumonia	17	With the exception of CO, all pollutants were associate with pneumonia hospitalization (PM₁₀: ER, 1.5%, 95% CI, 0.6% to 2.4% per 10 μg/m³; PM₁₀: ER, 1.8%, 95% CI, 0.5% to 3.1% per 10 μg/m³; SO₂: ER, 2.9%, 95% CI, 0.4% to 5.3% per 10 ppb; O₃: ER, 1.7%, 95% CI, 0.5% to 2.8% per 10 ppb; NO₂: ER, 1.4%, 95% CI, 0.4% to 2.4% per 10 ppb; CO: ER, 0.9%, 95% CI, 0% to 1.9% per 1,000 ppb)

FEV1, forced expiratory volume in one second; CI, confidence interval; LRS, lower respiratory symptoms; PEF, peak expiratory flow; OR, odds ratio; TRAP, traffic-related air pollution; RR, relative risk; ER, excessive risk.

^a) No. of articles included in the meta-analyses (note that the number of articles can vary by air pollutants and outcomes).

Table 2.

Summary of existing meta-analyses of correlation between air pollution and adverse birth outcomes

Study	Pollutant	Exposure period	Outcome	No. of articles^a)	Main result
Guo et al., 2019 [43]	PM₁₀, PM_2.5, NOx, NO₂, SO₂, O₃, CO	Entire pregnancy	Low birth weight	20	Increase in PM₁₀, NO₂, NOx,SO₂ was associated with increasing risk of low birth weight (PM₁₀: OR, 1.05, 95% CI, 1.02 to 1.09 per 20 μg/m³; NO₂: OR, 1.02, 95% CI, 1.00 to 1.04 per 20 ppb; NOx: OR, 1.03, 95% CI, 1.01 to 1.05 per 20 ppb; SO₂: OR, 1.21, 95% CI, 1.08 to 1.35 per 5 ppb)
			Preterm birth	24	Increase in PM₁₀, NOx, O₃, CO was associated with increasing risk of preterm birth (PM₁₀: OR, 1.05, 95% CI, 1.02 to 1.07 per 10 μg/m³; NOx: OR, 1.02, 95% CI, 1.01 to 1.03 per 20 ppb; O₃: OR, 1.04, 95% CI, 1.00 to 1.07 per 20 ppb; CO: OR, 1.06, 95% CI, 1.04 to 1.08 per 1 ppm)
			Small for gestational age	8	Increase in PM_2.5 and NO₂ was associated with increasing risk of small for gestational age (PM_2.5: OR, 1.01, 95% CI, 1.00 to 1.03 per 10 μg/m³; NO₂: OR, 1.02, 95% CI, 1.01 to 1.03 per 20 ppb)
Li et al., 2017 [44]	PM_2.5	Entire pregnancy	Term low birth weight	15	Increase in PM_2.5 was associated with increasing risk of term low birth weight (PM_2.5: OR, 1.03, 95% CI, 1.02 to 1.03 per IQR increase)
Li et al., 2017 [44]	PM_2.5	Entire pregnancy	Preterm birth	14	Increase in PM_2.5 was associated with increasing risk of preterm birth (PM_2.5: OR, 1.03, 95% CI, 1.01 to 1.05 per IQR increase)
Siddika et al., 2016 [45]	PM₁₀, PM_2.5, NO₂, SO₂	Entire pregnancy	Still birth	13	Increase in PM₁₀, PM_2.5, NO₂, SO₂ was associated with increasing risk of still birth, but not statistically significant (PM₁₀: OR, 1.014, 95% CI, 0.948 to 1.085 per 10 μg/m³; PM_2.5: OR, 1.021, 95% CI, 0.996 to 1.046 per 4 μg/m³; NO₂: OR, 1.066, 95% CI, 0.965 to 1.178 per 10 ppb; SO₂: OR, 1.022, 95% CI, 0.984 to 1.062 per 3 ppb)
Lamichhane et al., 2015 [46]	PM₁₀, PM_2.5	Entire pregnancy	Birth weight	28	Increase in PM₁₀ and PM_2.5 was associated with change in birth weight (PM₁₀: change in birth weight (g) –10.31, 95% CI, –13.57 to –7.05 per 10 μg/m³; PM_2.5: change in birth weight (g) –22.17(g), 95% CI, –37.93 to –6.41 per 10 μg/m³)
Lamichhane et al., 2015 [46]	PM₁₀, PM_2.5	Entire pregnancy	Preterm birth	18	Increase in PM₁₀ and PM_2.5 was associated with increasing risk of preterm birth (PM₁₀: OR, 1.23, 95% CI, 1.04 to 1.41 per 10 μg/m³; PM_2.5: OR, 1.14, 95% CI, 1.06 to 1.22 per 10 μg/m³)
Sun et al., 2015 [47]	PM_2.5	Entire pregnancy	Preterm birth	18	Increase in PM_2.5 was associated with increasing risk of preterm birth (PM_2.5: OR, 1.13, 95% CI, 1.03 to 1.24 per 10 μg/m³)
Zhu et al., 2015 [48]	PM_2.5	Entire pregnancy	Birth weight	11	Increase in PM_2.5 was associated with change in birth weight (PM_2.5: change in birth weight (g) –14.58, 95% CI, –9.86 to –19.31)
			Low birth weight	7	Increase in PM_2.5 was associated with increasing risk of low birth weight (PM_2.5: OR, 1.05, 95% CI, 1.10 to 1.20 per 10 μg/m³)
			Preterm birth	12	Increase in PM_2.5 was associated with increasing risk of preterm birth (PM_2.5: OR, 1.10, 95% CI, 1.03 to 1.18 per 10 μg/m³)
			Small for gestational age	9	Increase in PM_2.5 was associated with increasing risk of small for gestational age (PM_2.5: OR, 1.15, 95% CI, 1.10 to 1.20 per 10 μg/m³)
			Still birth	1	No significant risks of still birth (PM_2.5: OR, 1.18, 95% CI, 0.69 to 2.04 per 10 μg/m³)
Sapkota et al., 2012 [49]	PM₁₀, PM_2.5	Entire pregnancy	Low birth weight	15	Increase in PM₁₀ and PM_2.5 was associated with increasing risk of low birth weight, but not statistically significant (PM₁₀: OR, 1.02, 95% CI, 0.99 to 1.05 per 10 μg/m³; PM_2.5: OR, 1.09, 95% CI, 0.90 to 1.32 per 10 μg/m³)
Sapkota et al., 2012 [49]	PM₁₀, PM_2.5	Entire pregnancy	Preterm birth	14	Increase in PM₁₀ and PM_2.5 was associated with increasing risk of preterm birth (PM₁₀: OR, 1.02, 95% CI, 0.99 to 1.04 per 10 μg/m³; PM_2.5: OR, 1.15, 95% CI, 1.14 to 1.16 per 10 μg/m³)
Stieb et al., 2012 [50]	PM₁₀, PM_2.5, NO₂, SO₂, O₃, CO	Entire pregnancy	Birth weight	30	Increase in PM₁₀, PM_2.5, NO₂ was associated with change in birth weight (PM₁₀: change in birth weight (g) -16.77, 95% CI, -20.23 to -13.31 per 20 μg/m³; PM_2.5: change in birth weight (g) -23.4, 95% CI, -45.5 to -1.4 per 10 μg/m³; NO₂: change in birth weight (g) -28.1, 95% CI, -44.8 to -11.5 per 20 ppb)
			Low birth weight	26	Increase in PM₁₀, NO₂, SO₂, CO was associated with increasing risk of low birth weight (PM₁₀: OR, 1.10, 95% CI, 1.05 to 1.15 per 20 μg/m³; NO₂: OR, 1.05, 95% CI, 1.00 to 1.09 per 20 ppb; SO₂: OR, 1.03, 95% CI, 1.02 to 1.05 per 5 ppb; CO: OR, 1.07, 95% CI, 1.02 to 1.12 per 1 ppm)
			Preterm birth	20	Increase in PM_2.5 was associated with increasing risk of preterm birth (PM_2.5: OR, 1.16; 95% CI, 1.07 to 1.26 per 10 μg/m³)

OR, odds ratio; CI, confidence interval; IQR, interquartile range.

^a) No. of articles included in the meta-analyses (note that the number of articles can vary by air pollutants and outcomes).

Table 3.

Summary of existing studies of correlation between air pollution and neurodevelopmental outcomes

Study	Pollutant	Exposure period	Outcome	No. of articles^a)	Main result
Lovasi et al., 2014 [77]	PAH	Prenatal (3rd trimester of pregnancy)	Cognitive test score	-	Prenatal PAH exposure above the median (2.26 ng/m³) predicted 3.5 points lower total WPPSI-R scores and 3.9 points lower verbal scores
Edwards et al., 2010 [78]	PAH	Pr enatal (2nd or third trimester)	Cognitive test score	-	Prenatal PAH exposure above the median (17.96 ng/m³) was associated with 1.4 points lower RCPM scores at 5 years of age
Perera et al., 2009 [80]	PAH	Prenatal (3rd trimester)	Cognitive test score	-	Prenatal PAH exposure above the median (2.26 ng/m³) was associated with 4.32 points lower full-scale IQ and 4.67 points lower verbal IQ scores
Porta et al., 2016 [81]	NO₂, PM	Prenatal/postnatal	Cognitive test score	-	A 10 μg/m³ increase of NO₂ exposure during pregnancy was associated with 1.4 points lower verbal IQ and 1.4 points lower verbal comprehension IQ scores at 7 years of age
Guxens et al., 2014 [82]	NO₂, PM	Prenatal	Cognitive and psychomotor development test score	-	A 10 μg/m³ increase of NO₂ exposure during pregnancy was associated with 0.68 points lower global psychomotor development score at 1–6 years of age, but not with cognitive development
Kim et al., 2014 [83]	NO₂, PM₁₀	Prenatal (entire pregnancy)	Neurodevelopment test score	-	A 10 ppb increase of NO₂ exposure during pregnancy was associated with 3.12 points lower mental developmental index (MDI) and 3.01 points lower psychomotor developmental index (PDI). A 10 μg/m³ increase of PM₁₀ exposure was associated with 4.60 points lower MDI and 7.24 points lower PDI at 6 months of age, but not at 12 or 24 months of age
Perera et al., 2012 [79]	PAH	Prenatal (3rd trimester)	Behavioral problem	-	Prenatal PAH exposure above the median (2.27 ng/m³) or maternal and cord adducts (detectable or higher) was associated with symptoms of anxious/depressed and attention problems
Min and Min, 2017 [86]	NO₂, PM₁₀	Prenatal+postnatal	ADHD	-	A 1 μg/m³ increase of NO₂ and PM₁₀ exposure was associated with incidence of childhood ADHD (NO₂: HR, 1.03, 95% CI, 1.02 to 1.04; PM₁₀: HR, 1.18, 95% CI, 1.15 to 1.21)
Newman et al., 2013 [84]	ECAT	Postnatal	ADHD symptoms	-	Exposure to highest tertile of ECAT (≥0.40 μg/m³) during child’s first year of life was associated with hyperactivity T-scores in the at risk range at 7 years of age (OR, 1.70; 95% CI, 1.15 to 1.21)
Forns et al., 2016 [85]	EC, BC, NO₂	Postnatal	ADHD symptoms	-	Exposure to TRAPs exposure were not associated with ADHD symptoms scores
Lam et al., 2016 [87]	PM₁₀, PM_2.5	Prenatal+postnatal	ASD	23	A 10 μg/m³ increase of PM₁₀ and PM_2.5 exposure was associated with ASD (PM₁₀: OR, 1.07; 95% CI, 1.06 to 1.08; PM_2.5: OR, 2.32; 95% CI, 2.15 to 2.51)
Flores-Pajot et al., 2016 [88]	NO₂, PM₁₀, PM_2.5, O₃	Prenatal/postnatal	ASD	12	A 10 ppb increase of NO₂ exposure during pregnancy was associated with ASD (RR, 1.05; 95% CI, 0.99 to 1.11). A 10 μg/m³ increase of PM_2.5 exposure during pregnancy was associated with ASD (RR, 1.34; 95% CI, 0.83 to 2.17)

OR, odds ratio; CI, confidence interval; IQR, interquartile range.

^a) No. of articles included in the meta-analyses (note that the number of articles can vary by air pollutants and outcomes).

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