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Long-Term (2003–2019) Air Quality, Climate Variables, and Human Health Consequences in Dhaka, Bangladesh

Long-term trends in air quality by studying the criteria pollutants (PM2.5, PM10, CO, O3, NO2, and SO2) and climate variables (temperature, surface pressure, and relative humidity) were depicted in this study. The 17-year (2003–2019) average values of PM2.5, PM10, CO, O3, NO2, and SO2 were 88.69 ± 9.76 μg/m3, 124.57 ± 12.75 μg/m3, 0.69 ± 0.06 ppm, 51.42 ± 1.82 ppb, 14.87 ± 2.45 ppb, and 8.76 ± 2.07 ppb, respectively. The trends among the ambient pollutants were increasingly significant (p < 0.05) except for O3 with slopes of 1.83 ± 0.15 μg/m3/year, 2.35 ± 0.24 μg/m3/year, 0.01 ± 0.002 ppm/year, 0.47 ± 0.03 ppb/year, and 0.40 ± 0.02 ppb/year for PM2.5, PM10, CO, NO2, and SO2, respectively. Pearson correlations revealed a significant association among the pollutants while a noteworthy correlation was observed between ambient pollutants and surface temperature. Principal component analysis (PCA) and positive matrix factorization (PMF) have been employed collectively to examine the main sources of the pollutants. PCA revealed similar trends for PMs and CO, as well as NO2 and SO2 being equally distributed variables. PMF receptor modeling resulted in attributing four sources to the pollutants. The factors inferred from the PMF modeling were signified as vehicular emissions, road/soil dust, biomass burning, and industrial emissions. The hazard quotient (HQ) values were not antagonistic (HQ < 1) in acute exposure levels for the three age groups (infants, children, and adults) while showing significant health risk (HQ > 1) in chronic exposure for infants and children. Children are identified as the worst sufferers among the age groups, which points to low breathing levels and high exposure to traffic pollution in Dhaka, Bangladesh.


INTRODUCTION
Air pollution and climate change are the two most significant and interconnected challenges plaguing the 21st century. If existing policies remain unchanged, air pollution would be the most important environmental factor affecting premature deaths by 2050 (OECD, 2012). Global warming has culminated in a 43% increase in anthropogenic radiative forcing (RF) since 2005, according to the new IPCC report, focusing on human behavior as the most significant influencer (Stocker et al., 2013). The urban heat-island effect causes towns to be far warmer than their neighboring rural area due to enhanced anthropogenic activities. Owing to associations between warming and air emissions, this effect would pose extreme health problems for cities around the world by 2050 (Schmale et al., 2014). Lancet Commission on Pollution and Health reported 6.5 million deaths in 2015 due to atmospheric air pollution (Landrigan et al., 2017). while mortality due to past climate change on air quality was much lower: ∼1500 and ∼2200 deaths per year due to ozone and PM 2.5 , respectively (Silva et al., 2013). The global air quality scenarios are unlikely to change anytime soon, and the crisis in the megacities of developing countries is expected to worsen. As a result, it is important to continue tackling air quality problems in tandem with climate change mitigation initiatives (Williams, 2012).
Approximately 91% of the world's population live in areas where WHO air quality standards have been exceeded. However, due to its large population, Bangladesh is one of the most polluted countries in terms of air quality, with Dhaka ranking as one of the world's two most polluted cities (AirVisual, 2018). In Bangladesh, there had been little to no effort and administrative works to track or mitigate ambient air pollution before 1999. In 1999, the government began establishing frameworks and regulations to meet US EPA and Bangladesh National Air Quality Standards, especially in Dhaka. In this regard, a number of controls have been implemented, including the prohibition of leaded gasoline in July 1999 and the replacement of old two-stroke engine three-wheelers with compressed natural gas (CNG)-powered four-stroke three-wheelers beginning in January 2003; introducing CNG-powered cars, buses, and trucks; and regulating brick kiln emanations, which resulted in a reduction of airborne Pb concentrations and improved air quality than before (Salam et al., 2013;Begum and Hopke, 2019). However, since the introduction of CNG and the prohibition of two-stroke engines, traffic congestion in Dhaka city has greatly worsened air quality, and numerous brick kilns using crude oil, fossil fuel, coal, natural gas, electricity, and biomass as a source of energy have sprung up all over the city and have been discharging many air pollutants including black carbon and organic carbon (Salam et al., 2013). In addition, research on the results of CNG conversion in other megacities (Rio de Janeiro, Mexico City, and New Delhi) and the greenhouse gas (GHG) benefits of such conversion showed that switching from diesel vehicles increased high-emission particulates and black carbon, which are more potent as GHGs than CO 2 or CH 4 . Thus, large-scale conversion of petrol vehicles embodies the risk of reduced GHG benefit or even negative GHG impacts (Wadud and Khan, 2013). Furthermore, permanent wetlands have been disappearing at an unprecedented pace as a result of unplanned urbanization to accommodate the huge population, with more than 49% of wetland areas disappearing in Dhaka city between 1960 and 2008 (Rai et al., 2017). As a result of such adverse situations, Dhaka had very high (>1) toxicity potential (TP) values of PM 2.5 and PM 10 (Zaman et al., 2021) and recorded the highest mortality and morbidity rates (hospital admissions) among the megacities studied, with about 7,000 deaths and 2,100 excess cases (cardiovascular and respiratory) each year (Gurjar et al., 2010). Table 1 reports several previous researches on ambient air quality and climate impact in Dhaka, Bangladesh, undertaken after 2003. Carbon monoxide, lead, ground-level ozone, particulate matter (PM), nitrogen dioxide, and sulfur dioxide have been designated as criteria air contaminants by the Environmental Protection Agency (EPA) and the World Health Organization (WHO), and national and global ambient air quality standards (NAAQS) have been developed for these six pollutants (EPA). These contaminants, which are made up of various materials, have a broad range of sources of pollution and varying degrees of health impacts and toxicity, dictating the use of source apportionment studies to understand the formation processes and their sources. On source apportionment, two chemometric techniques, principal component analysis (PCA) and positive matrix factorization (PMF) receptor model, were employed collectively. PCA is utilized to relate the air pollutants and their overall changes in the aerosol composition while PMF is used to determine the different sources of pollution and the temporal variability of each pollutant without considering their correlations (Padoan et al., 2020).
Dhaka is one of the most contaminated cities in the world and is in dire need of effective mitigation policies to attain national and global air quality standards. Unfortunately, there is limited information for the criteria air pollutants levels, sources apportionment, impact on human health, and climate variables based on long-term datasets. Therefore, the objective of this study is to understand the long-term (2003-2019) evolution of major atmospheric contaminants (PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 ) and the effect of meteorological parameters (temperature, pressure, and relative humidity) on these pollutants following the January 2003 ban on old two-stroke engine three-wheelers in favor of CNG-powered four-stroke three-wheelers. Although there have been recent comparative studies for fine and coarse fractions of PM in terms of source attribution in the seasonal and short-term periods, long-term studies for all of the criteria contaminants and their health effects, as well as their origins, have been scarce. This study will help evaluate the aftermath of implementing the CNG-powered vehicles and how the vehicles and other sources might be regulated in the future to improve the ambient air quality in Dhaka, Bangladesh.

Description of the Study Area
Dhaka, Bangladesh's capital and most populous city, is situated at the northeastern end of the Indo-Gangetic Plain (IGP). Dhaka is the center of Bangladesh with an elevation of ∼9 m above sea level (Figure 1). Dhaka encompasses a total area of 1463.60 square kilometers (565.10 square miles) and possesses a population of 12.5 million and, hence, is one of the most densely populated cities in the world with a density of 8,229 per square kilometer. Dhaka has a population growth rate of 3.48% per year due to ever-growing urbanization (urbanization rate = 77.36%), which drives a huge chunk of the population toward urban life every year from rural/suburban areas (www.dhaka.gov.bd). As  (∼USD 17.7 million) were in the order of magnitude less than the air quality gains.
GIS-based modeling Wadud and Khan, 2013 Climate variables (monthly rainfall and temperature) Daily energy usage in Dhaka city rises by 6.46-11.97 and 2.37-6.25 MkWh per unit increase in temperature and rainfall, respectively, while daily gross residential energy demand and peak demand will rise by 5.9-15.6% and 5. a result, Bangladesh with a mean PM 2.5 concentration of 77.1 µg/m 3 and megacity Dhaka with the same mean concentration of that of Bangladesh has emerged as the 1st and 2nd most polluted country and capital city in the world (Amato et al., 2020).

Air Pollution and Meteorological Data
Although

CAMS Reanalysis Data
Reanalysis combines model data with measurements from around the world to construct a globally robust and coherent resource using a physics and chemistry-based model of the atmosphere. The data integration is defined as a technique used by numerical weather prediction centers and air quality forecasting centers, in which a preceding prediction is merged with currently available measurements in an optimized way every so many hours (12 h at ECMWF) to create a new best estimate of the atmospheric situation, known as analysis, from which an updated, enhanced forecast is produced (ads.atmosphere.copernicus.eu). The CAMS reanalysis is the most recent global reanalysis data collection of atmospheric composition (AC) developed by the Copernicus Atmosphere Monitoring Service, and it consists of three-dimensional time-consistent AC fields, including aerosols, chemical species, and greenhouse gases, through the CAMS global greenhouse gas reanalysis (EGG4). The dataset improves on the knowledge obtained during the development of the Monitoring Atmospheric Composition and Climate (MACC) reanalysis and the CAMS interim reanalysis. The assimilation method estimates observational biases and separates high-quality data from lowquality data. Estimates are made using the atmosphere model in places where data collection is limited or for pollutants for which no direct measurements are possible. Reanalysis is a very easy and common dataset to work with since it provides forecasts at each grid point across the world at each daily production time, over a long period of time, and in the same format. The CAMS reanalysis was created with 60 hybrid sigma/pressure (model) levels in the vertical, with the top level at 0.1 hPa, using 4DVar data assimilation in ECMWF's Integrated Forecast System (IFS) CY42R1. The 4DVar data assimilation employs 12-h assimilation periods spanning 09 UTC to 21 UTC and 21 UTC to 09 UTC, respectively. The IFS model documentation for various model cycles can be found at https://www.ecmwf.int/en/forecasts/documentation-andsupport/changes-ecmwf-model/ifs-documentation. On these levels, atmospheric data are available, which are also interpolated to 25 strain, 10 potential temperature, and 1 potential vorticity level(s). Data on the "surface" or "single stage" are also available.
EAC4 is the fourth-generation ECMWF global reanalysis of AC. Monthly surface data were utilized to study human exposure to the selected pollutants and the effect of the climate variables. Monthly means for assessments and instantaneous predictions are calculated using data with a valid time in the month, ranging from 00 to 23 UTC, except the time 00 UTC on the first day of the next month. Data with a prediction date that falls within the month are used to establish monthly means for accumulations and mean rates.
However, there have been some issues associated with assimilation of the CAMS global reanalysis (EAC4). During 2003 and between March and August 2004, the ozone analysis has a degraded quality, while from 2013 onwards, there is a larger seasonally varying bias in ozone in the free troposphere, particularly in the Arctic and Antarctic that is not seen in the control run. Furthermore, NO 2 in the CAMS reanalysis is mainly influenced by prescribed emissions (e.g., anthropogenic MACCity, GFAS biomass burning) and only to a lesser extent by assimilated findings due to its short lifespan. As a result, patterns or deviations derived from NO 2 reanalysis fields will primarily represent trends in underlying pollution. More details about the EAC4 data products, i.e., the observation techniques, data assimilation methods, bias correction, etc. have been described by Inness et al. (2019) and Flemming et al. (2015).

Validation of the Reanalysis Data
The CAMS-84 is a sub-project of CAMS that deals with service product validation. The validation reports for the global and regional services are updated every 3 months by CAMS-84. The validation is focused on a variety of measurements and measuring methods, including in situ observations, surface remote sensing, airplane observations, balloon sounding, ship observations, and satellite observations. With a deadline of ∼1 month after sensing, the validation reports' three-monthly interval adds restrictions on the timely availability of the findings. Table 2 represents the assimilation and validation products for specific species along with their vertical range. The validation reports and the verification websites can be found at http://atmosphere.copernicus.eu/usersupport/validation/verification-global-services. For this study, the selected reanalysis products were validated with the monthly average air pollution concentration data overlapping the months of the analysis period obtained from the Department of the Environment (DoE, CASE project) in Dhaka, Bangladesh. Validation of PM 2.5 and PM 10 NO 2 , and SO 2 with the DoE data has been depicted in the following figure and the concentrations showed R 2 values of 0.93, 0.85, 0.58, and 0.76, which confirms that the reanalysis data are capable of reflecting the ground-based air pollution data (Figure 2). Validation for the other pollutants was not done due to temporal anomalies between the reanalysis and ground-based data.

Source Apportionment Using PCA and PMF Modeling
Correlations among the variables were studied through Pearson correlation coefficients instead of non-parametric tests as nonparametric tests are better suited for datasets having no linear relationships or violating normality (Hauke and Kossowski, 2011). Source apportionment has always been tricky in the case of environmental datasets (Gao et al., 2016). PCA has been used robustly (Cotta et al., 2020) and coupled with other techniques (Sun and Sun, 2017;Franceschi et al., 2018;Gao et al., 2020;Liu et al., 2020). On the other hand, the contribution of various sources to PM and other contaminants around the world have been studied by PMF analysis, as well as references therein (Cesari et al., 2016(Cesari et al., , 2018Sharma et al., 2016a,b;Crilley et al., 2017;Liu et al., 2017;Ryou et al., 2018;Jain et al., 2019Jain et al., , 2020. Although PCA is useful for evaluating the association between variables and measurements, it can also be used to describe each observation independently, whereas PMF is more based on the overall dataset definition. As a result, PCA can be used to explain how each attribute affects the observations, as well as whether certain observations or classes of observations have unusual characteristics. Instead of focusing on each observation or indicator, PMF explores the temporal pattern of all variables to find a potential common source. As a result, combining PCA and PMF to achieve an aggregate statistical summary of data is a safe way to view each observation as "independent" and as part of a temporal pattern (Padoan et al., 2020).
Firstly, the distribution of the variables over the studied period was evaluated through PCA, a widely used chemometric technique (Jollife and Cadima, 2016). PCA allows rotating the space spanned by the original variables to a new space spanned by the principal components (PCs), in which the first (generally two or three) PCs report the majority of the details found in the original data. As a result, analyzing the behavior of samples (in the scores plot) and variables is made easier by visualizing the two-or three-dimensional plot of PC1 vs. PC2 (and/or PC3) (in the loading plot).
Then, PMF modeling was employed for the allocation of sources and the inner characteristics of ambient air pollutants (PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 ) on a monthly basis using EPA PMF (version 5.0). PMF also rotates space spanned by the original variables but the calculated factors are not orthogonal to each other like PCA. This way, a better or worse solution can be obtained by PMF modeling by rotating the variables. Standard deviations associated with each measurement are also required to choose the most suitable number of factors and to evaluate the rotational stability of the obtained solution in the PMF analysis (Paatero and Tapper, 1994). PMF allows for the visualization of diverse sources of air contaminants as well as their contributions to specific pollutant concentrations. Several previous research and related sources enumerated in those publications had detailed explanations of PMF algorithms and their use (EPA PMF 5.0 guide; Sharma et al., 2016a;Cesari et al., 2018;Jain et al., 2020). Therefore, only the compulsory information to elucidate PMF modeling has been described here.
The PMF decomposes a matrix composed of the factors (p), source profiles (f ), and the contribution (g) of each source to individual samples based on the following equation (Liu et al., 2017): where ij signifies species residuals, i is the number of concentrations, j is the number of chemical components, and X denotes i by j matrix.
Monthly average concentrations of the ambient air pollutants were utilized in the PMF modeling. To attain acceptable results reducing the uncertainties of online datasets, the following precautions were employed: (1) purging of the outliers (far-off values compared to the average value); (2) apportionment of the sources from monthly datasets (using daily mean concentrations obtained from hourly values); and (3) employment of multiple receptor model (Belis et al., 2015;Cesari et al., 2016). Photochemical oxidation of carbon monoxide (CO) and volatile organic compounds (VOCs) in the presence of nitrogen oxides (NO x = NO + NO 2 ) and sunlight is the primary source of ozone (Lu et al., 2018). Thus, including O 3 concentrations could bias the source apportionment of the receptor models by using PMF. Therefore, O 3 was excluded from the input dataset in the modeling.
Standard deviations for each month were included to account for uncertainties of each data point and ease the model to estimate results with a significant confidence level for each pollutant. PMF has the establishment of considering uncertainties accompanying each chemical component of the data (EPA PMF 5.0 guide).
where Error fraction is defined as a measure of the standard deviation of particular pollutants divided by the square root of the total number of concentrations. The signal-to-noise (S/N) ratio is utilized to categorize quality of data and the S/N ratios found in this study fall within the acceptable range of those presented in many PMF studies (Sharma et al., 2016a;Cesari et al., 2018;Amato et al., 2020;Jain et al., 2020). The data used in the modeling were specifically divided into three groups based on S/N ratios, with variables with S/N ratios of >2 being labeled as "strong variables, " variables with S/N ratios of 0.2-2 being labeled as "weak variables, " and the model employing three-fold uncertainty with them. Variables that had S/N ratios <0.2 were disregarded from further analysis and denoted as "bad variables" (Amato et al., 2020). The S/N ratio of all the variables of the air pollutants has been reported in Supplementary Table 1. PMF modeling was employed to run in robust mode, and the Q robust and Q true values were found to be in good agreement with the base run for a four-factor solution. Supplementary Table 2 displays the Q robust and Q true values for the base runs. The little discrepancies between the two Qvalues indicate that the models were able to achieve a satisfactory fit for the data and outliers. Furthermore, 100% convergence rate for all analytical runs was obtained in the model runs, which also affirms the steadiness of the model and the ability to fit all the variables suitably (Nayebare et al., 2018). Extra modeling uncertainty is an additional important parameter that pronounces the fitness of the model. No (0%) error constant (extra modeling uncertainty) was found for all the air pollutants. The results obtained for the air pollutants by PMF modeling had a significant agreement between measured and modeled concentrations specified by R 2 that further confirmed that the concentrations were well-reconstructed (Cusack et al., 2013). R 2 values [from the one-way analysis of variance (ANOVA) F-test] for all the air pollutants were detected to be higher than 0.98, and p-values [from the two-sample Kolmogorov-Smirnov (KS) test] were close to 0 (Supplementary Table 2). The performance factor profiles' uncertainties were also assessed using error estimation methods, namely, the Bootstrap (BS) and Displacement (DISP) methods. Details about error estimation methods used in EPA PMF software, 5.0, have been described by Brown et al. (2015). A strong mapping of the PMF species was observed for all datasets in the BS study, with unmapped cases accounting for <5% of the total. Furthermore, the findings are consistent since no factor profile swap was observed in DISP for any of the datasets (Manousakas et al., 2017).

Human Health Risk Assessment
Adverse effects due to exposure to toxic agents can be inclusively estimated through health risk assessment (USEPA, 1989). This procedure predicts effects on human health caused by a particular pollutant utilizing existing exposure data (WHO, 1996). Exposure to PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 and their adverse effects has been studied in this study through the US EPA human health risk assessment framework. This method has been employed in several previous studies to assess non-carcinogenic risk due to the criteria pollutants (Megido et al., 2017;Piersanti et al., 2018;Embiale et al., 2020;Mundackal and Ngole-jeme, 2020;Edlund et al., 2021;Morakinyo et al., 2021). The four steps involved in the HHRA are depicted below:

Hazard Identification
Firstly, PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 have been identified as criteria air pollutants by the WHO as well as USEPA (World Health Organization, 2005;USEPA, 2016).

Dose-Response Assessment
Secondly, the amount of pollutants absorbed by the body was calculated as a function of concentration and exposure time. This research did not have a dose-response analysis. Rather, WHO and the DoE environmental quality guidelines for these air contaminants were used as a benchmark in this study (depicted in Table 3).

Exposure Assessment
Then, identification of the exposed population and the magnitude of hazard and duration of exposure are estimated through exposure assessment. Inhalation is considered the major route of exposure to pollutants. Chronic (annual) and acute (1h) exposure assessments were determined for three different age groups, namely, infants (birth to a year), children (6-12 years), and adults (19-75 years). The acute exposure assessment for the non-carcinogenic pollutants (PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 ) was based on the rate equation as follows: where AHD stands for average hourly dosage for inhalation (µg/kg/h), C stands for chemical concentration (µg/m 3 ), IR stands for inhalation rate (m 3 /hour), and BW stands for bodyweight (kg) (WHO, 1999). The rate equation for the chronic exposure assessment for the non-carcinogenic pollutants (PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 ) was: where ADD represents the average daily dosage of the chemical of interest (µg/kg/day), C represents the volume of the chemical in ambient air (µg/m 3 ), IR represents the inhalation rate (m 3 /day), ED represents the exposure period (days), BW represents the exposed group's body weight (kg), and AT represents the averaging time (days) (WHO, 1999). ED is defined by the following equation: where ET denotes exposure time (h/day), EF denotes exposure frequency (days/year), and DE denotes exposure period (year). Table 4 shows the estimated values of each variable used in this assessment for each population group in terms of acute and chronic exposure periods (Morakinyo et al., 2017(Morakinyo et al., , 2021Embiale et al., 2020).

Risk Characterization
Finally, using the hazard quotient (HQ), the potential noncarcinogenic consequences of exposure to a known pollutant are quantified via the "Risk characterization" process (Morakinyo et al., 2017). HQ expresses the likelihood of a negative health outcome among stable and/or sensitive people. The adverse health outcome occurring among different individuals of different age groups is reflected by this process. Thus, noncancer risks associated with the air pollutants were estimated through HQ. Acute and chronic non-cancer risks were calculated according to the following equations: where RfC is an approximation containing uncertainty of considerable scale of an incessant inhalation exposure to the human population (including sensitive subgroups) that possesses a substantial risk of lethal effects during a lifetime (www.epa.gov). The chemical identifications, RfC values, and affecting organs are presented in Supplementary Table 2.
An HQ value of 1.0 indicates no risk to human health, while an HQ value of 1.0 indicates a marginal risk, indicating that the considered contaminant is not a potential health risk, to even a sensitive person. However, an HQ > 1.0 signifies risks to some extent upon exposure to different individuals, adults, and/or children (USEPA, 1989).

Ambient PM Trends in Dhaka
Long-term yearly as well as monthly trends of PM 2.5 and PM 10 have been depicted in Figure 3. Supplementary Table 4 shows the statistics of PM 2.5 and PM 10 during the studied period. Both PM 2.5 and PM 10 showed normal distribution for the studied period with mean yearly concentrations of 88.69 ± 9.76 and 124.57 ± 12.75 µg/m 3 , respectively. The yearly values of PM 2.5 and PM 10 exceeded the national air quality standards respectively by nearly 6.0 and 2.5 times while exceeding WHO standards by 9.0 and 6.0 times. The linear regression analysis has been performed to determine the trends and statistical significances of PM 2.5 and PM 10 . Increasing trends have been observed for PM 2.5 and PM 10 over the years with slopes of 1.83 ± 0.15 and 2.35 ± 0.24 µg/m 3 /year, respectively. One-way ANOVA showed that the increasing trends were statistically significant (p < 0.05) for both the PMs (Figure 3). Rana et al. (2016) reported similar findings in Dhaka that showed that PM 2.5 concentrations exceeded the WHO guideline value by 8-13 times. Begum and Hopke (2018) also showed that long-term trends for PM 2.5 and PM 10 exceed the USEPA standards in Dhaka.
Monthly variations were identical for the PMs with the highest values observed in winter (November-February) and the lowest in monsoon (June-August). Previous studies also supported such seasonality of PMs with the highest values being associated with the dry season compared to the wet season (Rana et al., 2016;Rahman et al., 2020).  Figure 1). NO 2 and SO 2 were below the annual national guideline values set by DoE. Yearly trends of CO, O 3 , NO 2 , and SO 2 showed slopes of 0.01 ± 0.002 ppm/year, 0.13 ± 0.09 ppb/year, 0.47 ± 0.03 ppb/year, and 0.40 ± 0.02 ppb/year for the studied period. One-way ANOVA showed that the trends of the trace gases were statistically significant (p < 0.05) except for O 3 (Figure 4).  showed similar significant positive trends for SO 2 and CO in Dhaka, Bangladesh for 2013-2017. Monthly observations showed that CO, NO 2 , and SO 2 followed an almost similar pattern over the year with the highest values in winter (November-February) and the lowest in monsoon (June-August). On the contrary, O 3 showed the maximum values in March-May and the minimum in July-September. The seasonal trends of ozone in Dhaka differed from those of other contaminants, which all exhibited distinct seasonal variation with a peak in the winter and a trough in the monsoon .

Meteorological Parameters' Trends in Dhaka
The air quality of an urban area is heavily influenced by meteorological factors Afrin et al., 2021). Long-term trends of the meteorological parameters have been depicted in Figure 5. Surface temperature, pressure, and relative humidity showed yearly values of 25.99 ± 0.750 • C, 1006.46 ± 0.54 hPa, and 71.30 ± 1.36%, respectively, over the studied period. Monthly variation of temperature showed the highest values in April-June and lowest in December-January. Surface pressure showed opposite monthly variation with the highest values observed in June-July and lowest in December-January. Relative humidity, on the other hand, showed the highest values in June-September and lowest in February-March. Linear regression of the parameters showed slopes of 0.12 ± 0.02 • C/year, 0.03 ± 0.02 hPa/year, and 0.11 ± 0.07%/year, respectively, for temperature, pressure, and RH. The one-way ANOVA study revealed that the trends were statistically insignificant except for temperature.

Correlation Among the Pollutants and Meteorological Parameters
Pearson correlation analyses were employed to quantify relationships among the ambient air pollutants and meteorological parameters as the variables did not violate the normality test (Table 5; Supplementary Figure 1). PM 2.5 and PM 10 showed significant positive values with PMs, NO 2 , and SO 2 . Furthermore, NO 2 and SO 2 also showed significant positive values with each other, PMs, and CO. The significant positive correlations among the air pollutants suggested similar production pathways for them.
Previous studies also investigated associations among the air pollutants and meteorological parameters. Ozone had nonsignificant associations with the other pollutants, according to . Although not significant, O 3 has a positive association with PMs, CO, NO 2 (R 2 > 0.37), suggesting that the other pollutants could play important roles in the development of O 3 . Besides, O 3 showed a negative correlation with RH but a positive correlation with temperature.
In the case of the meteorological parameters, temperature showed significantly positive correlations with all the pollutants but not in the case of the other meteorological variables. Surface pressure did not show any significant association with any other variables other than RH. Lastly, RH did not exhibit any significant connection with the variables. However, according to Afrin et al. (2021), air temperature, wind speed, and wind direction could account for more than 90% of PM 2.5 variability.

Principal Component Analysis
PCA was employed on the monthly datasets of the air pollutants. The datasets were auto-scaled before the analysis. This indicates that the column mean has been subtracted from each digit of the dataset, and the result has been separated by the column standard deviation. Figure 6 shows the bi-plots obtained by the PCA carried out on the datasets. It reports both scores and loadings in the same PC1 vs. PC2 graph. PC1 and PC2 loadings account for 98.88% of the total variance of the pollutants. PC1 carries 45.20, 45.20, 45.02, 44.09, and 44.09% of explained variance for PM 2.5 , PM 10 , CO, NO 2 , and SO 2 and PC2 carries 55.32 and 55.25% of explained variance for NO 2 and SO 2 (Figure 6). The two PMs, CO, NO 2 , and SO 2 have the same characteristics as they are distributed evenly along the x-axis, which accounts for almost ∼45% of the variance. Thereby, PC1 can be inferred to be vehicular emissions according to the component variance test, whereas NO 2 and SO 2 showed similar discrimination along the y-axis, contributing ∼55% of these variables. Thus, PC2 can be attributed to the industrial emissions enriched in NO 2 and SO 2 . Furthermore, the variables are almost evenly distributed in the positive and negative regions of PC1 and PC2. It indicates that the chemical composition of the studied compounds has similar concentrations in the case of these two variables.

PMF Modeling
The factor profiles of all the sources of the air pollutants (PM 2.5 , PM 10 , CO, NO 2 , and SO 2 ) are depicted in Supplementary Figure 2. Four factors were attributed to be   5 | Pearson correlation coefficients among the air pollutants (PM 2.5 , PM 10 , CO, NO 2 , and SO 2 ) and the meteorological parameters (surface temperature, pressure, and relative humidity).  the estimated sources contributing to the aforementioned ambient air pollutants. The percent contributions of the factors influencing the air pollutants have been depicted in Figure 7.
Factor 1: The first factor is characterized by the highest contribution (74.7%) to NO 2 followed by the signature of 36.5, 35.7, 20.5, and 19.7%, respectively, for PM 2.5 , PM 10 , CO, and SO 2 (Figure 7). Thus, factor 1 is inferred to be vehicular emissions as these pollutants were significantly correlated, suggesting similar sources. Despite the fact that many buses in Dhaka have been converted to CNG engines, heavy-duty trucks that are limited continue to run on diesel between the hours of 10 p.m. and 6 a.m. However, the lower contribution to SO 2 suggests that the conversion of most light-duty vehicles and buses to CNG has resulted in significant reductions in light-duty vehicle and bus emissions (Begum and Hopke, 2018).
Factor 2: PM loadings appeared to be highest (42.9 and 42.7%, respectively, for PM 2.5 and PM 10 ) for factor 2 with contributions of 28.5 and 22.5% for CO and NO 2 , suggesting that this factor can be inferred to be road/soil dust or secondary sources. Elemental characterization is needed to correctly attribute this factor to the ambient pollutants. Spearman correlation revealed that PMs have significant correlations with CO, NO 2 , and SO 2 that further affirms traces of the same factor in the case of these pollutants. Due to both anthropogenic and natural sources, dust has been identified as a significant contributor to measure PM 2.5 in Dhaka, accounting for 11% of total PM 2.5 (Weagle et al., 2018).
Factor 3: This factor is characterized by the highest contribution (50.5%) to CO with significant contributions to SO 2. PMs are also influenced by this factor with loadings of 14.2 and 15.1%, respectively, for PM 2.5 and PM 10 . This factor can be inferred to biomass or fossil fuel burning as suggested by the high loading of CO. Ommi et al. (2017) reported the transboundary influence of biomass burning from the IGP to be an important factor in Dhaka, mainly arising from the preparations of the lands through field burning. Furthermore, Salam et al. (2008) reported that the higher concentration of SO 2 in the city center is possibly due to the high content of sulfur in fossil fuel.
Factor 4: Factor 4 can be inferred as industrial emissions as it contributes mostly (39.2%) to SO 2 with traces in the case of CO (0.5%) and NO 2 (2.0%). Both PM 2.5 and PM 10 are associated with about 6.5% for factor 2. The high contribution to SO 2 from this factor signifies the effect of industrialization centered in Dhaka, which has increased exponentially in the last decade or so. The commercial areas of Dhaka had the highest SO 2 concentration (76.8 µg/m 3 ) (Salam et al., 2008).
However, since sources of atmospheric pollutants are extremely complicated and diverse, particularly for unorganized emission sources, ambient pollutants cannot be apportioned perfectly through receptor modeling, and some factors remain unknown (Liu et al., 2016(Liu et al., , 2017. Furthermore, the dearth of element analysis for metals limits the capability of receptor models to categorize all the sources present regionally. Moreover, the transboundary effects are also significant for ambient regional pollutants in Bangladesh that might affect the ambient air quality as reported by many previous studies (Rana et al., 2016;Rahman et al., 2020).

Human Health Risk Assessment
The HQ was calculated for three age groups (infant, child, and adult) in acute and intermediate level exposures, which have been reported in Figure 8. At the acute exposure level, no pollutants showed an adverse effect, that is, HQ values were below 1, for any of the age groups. On the other hand, the HQ values posed significant health risk (HQ > 1) at the chronic exposure level for infants and children while no antagonistic health effects risk (HQ < 1) were observed for the pollutants in the case of the adults. Among the pollutants, PM 2.5 (1.81 × 10 3 ± 2.00 × 10 2 ) and O 3 (1.03 × 10 3 ± 3.65 × 10 1 ) were observed to be the most harmful pollutants affecting the studied age groups, especially the children. In terms of the studied age groups, children were observed to be affected far more than infants and adults at the chronic exposure level. These results suggest that the air pollutants affect all age groups significantly when considered at the chronic level with children being the worst sufferers while negligible effects are observed at the acute level. Owing to a variety of factors, including their comparatively higher level of air inhalation (a resting infant's air consumption per weight unit is double that of an adult), their immune system and lungs not being fully grown, children are the population most impaired by indoor air contamination (Lina Thabethe et al., 2014). Morakinyo et al. also demonstrated a similar adverse impact on children when compared to other age groups. These results essentially signify that low breathing heights could be the main factor along with other indoor and outdoor air pollution sources behind this phenomenon in children who are particularly susceptible to ground-level pollution. In a study conducted at a local school, Sharma and Kumar (2020) found that in-pram babies are exposed to up to 44% higher fine particle concentrations than adults. Table 6 lists some more previous studies comparing health risks associated with ambient air pollutants.

DISCUSSION AND FUTURE IMPLICATIONS
The air pollutant (PM 2.5 , PM 10 , CO, NO 2 , and SO 2 ) concentrations except O 3 showed significantly increasing trends in this study. However, an analysis of Dhaka's air quality over two decades (1996)(1997)(1998)(1999)(2000)(2001)(2002)(2003)(2004)(2005)(2006)(2007)(2008)(2009)(2010)(2011)(2012)(2013)(2014)(2015) found that the city's air quality has remained constant over the last decade, despite increased economic development and the number of sources such as passenger cars and brick kilns (Begum and Hopke, 2018). On the contrary, a recent analysis found that PM 2.5 concentrations in Dhaka decreased slightly (statistically non-significant) from 2013 to 2017, but fine PM concentrations remained elevated and FIGURE 8 | Hazard quotients associated with the ambient pollutants (PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 ) for infants, children, and adults in chronic and acute levels. Children are more susceptible to non-cancer risks than adults and ingestion was identified as the dominant pathway (HI < 1).

Rahman et al., 2021
This study PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 HQ < 1 at acute levels but HQ > 1 for infants and children at chronic level presumably continue to affect human health . Therefore, there remains a need for further study into long-term seasonal cycles, as well as their assessment concerning actions taken by relevant bodies. Among the meteorological parameters, the temperature seemed to significantly correlate with the air pollutants (PM 2.5 , PM 10 , CO, NO 2 , and SO 2 ) except O 3 . However, according to Afrin et al. (2021), meteorological factors (temperature, relative humidity, etc.) account for about 57% and 35% of the variations in PM 2.5 and PM 2.5−10 concentrations, respectively, implying that the finer PM fraction is affected more by meteorology than the coarser fraction. Thus, more quantitative approaches to how climate change affects urban air quality may provide further insights into contaminant reduction policies.
This study estimates four probable main sources contributing to the emission of the six air pollutants in Dhaka, Bangladesh, which are vehicular emissions, road/soil dust, biomass burning, and industrial emissions. In a study on NO x pollution from vehicular emissions in Dhaka, Iqbal et al. (2019) found that, while a critical urban health ecosystem already exists, the current pattern of vehicular expansion, combined with current vehicle technology and on-road traffic management systems, may soon lead to an unbecoming situation. As a result of these findings, the vehicular management system in Dhaka should be strengthened, and further research into PMs, CO, and NO x emissions caused by them should be conducted. Furthermore, according to , ingestion of dust particles increases the risk of heavy metals (Cr, Cd) in children and adults in Dhaka City, where children were facing a possible health risk. Dhaka is witnessing several infrastructure schemes, such as the Dhaka Metrorail Project and the Dhaka Elevated Expressway Project, which have raised the risk of dust contamination by a factor of many. So, heavy metal contamination caused by dust particles should be investigated more thoroughly in Dhaka, as it poses a threat to children in particular. Rahman et al. (2020) suggested that air pollution in Dhaka is influenced by both local and transboundary sources, but biomass-related PM 2.5 was found to be the most prevalent during cycles of crop-burning in the IGP. Thus, biomass burning is a major contributor to Dhaka's poor air quality, necessitating further study into the source's impact and mitigation. Finally, the rising pattern of SO 2 in this study and previous studies  indicates that industrial operations in Dhaka, especially brick kiln operations and high sulfur diesel usages, are still contributing significantly to detrimental air quality. More studies encompassing the brick kiln operations and other industrial usage of high sulfur materials in Dhaka are also of paramount importance. Begum et al. (2011) described vehicular emissions and emissions from brick kilns as the two major sources of air pollution in Dhaka and stated that the government of Bangladesh is exploring various measures to minimize emissions from those sources through the adoption of regional policies. However, the pollutant patterns in this study indicate that effective implementation of such measures is still scarce in Dhaka, Bangladesh.

CONCLUSION
In this study, monthly ambient concentrations of the air pollutants (PM 2.5 , PM 10 , CO, O 3 , NO 2 , and SO 2 ) and meteorological data (temperature, surface pressure, and relative humidity) were utilized to explore long-term variations of these parameters and their association with each other. Longterm trends of the ambient pollutants were observed to be increasing significantly in the one-way ANOVA test except for surface ozone while the meteorological parameters showed no significant trends over the studied period. Pearson correlation studies revealed that the ambient pollutants were significantly (CI > 95%) correlated with each other, suggesting probably the same sources. The PCA bi-plot revealed that the PMs and CO demonstrated similar variance while NO 2 and SO 2 followed an analogous pattern. However, four factors emerged as estimated sources of the pollutants in PMF receptor modeling, which were vehicular emissions, road/soil dust, biomass burning, and industrial emissions. PMs were dominated (∼42%) by the road/soil dust along with emissions from vehicles. Biomass burning played a major role in CO (50.5%) and SO 2 (41.1%) production while industrial emissions were another prominent factor (39.2%) in the case of SO 2 . On the contrary, NO 2 was identified to be mainly emitted from vehicular emissions (74.7%).
Health risk assessment of the pollutants for three age groups (infant, child, and adult) in acute level exposures indicated no adverse effect (HQ < 1) for any of the age groups. On the other hand, the HQ values posed significant health risk (HQ > 1) at the chronic exposure level for infants and children while no antagonistic health effects risk (HQ < 1) were observed for the pollutants in the case of the adults.
This study reveals that the implementation of CNG wheelers in 2003 might have reduced Pb emissions in megacity Dhaka, but vehicular emissions along with road dust, biomass burning, and industrial emissions remain the most prominent sources that have a significant hazard risk on children and infants particularly. However, since most studies have focused on Dhaka, there is still room to assess long-term possible health risks and the effect of climate variables on air quality at the divisional and district levels in Bangladesh.

DATA AVAILABILITY STATEMENT
The raw data supporting the conclusions of this article will be made available by the authors, without undue reservation.

AUTHOR CONTRIBUTIONS
All authors listed have made a substantial, direct and intellectual contribution to the work, and approved it for publication.

ACKNOWLEDGMENTS
The authors acknowledge the support of the Department of Chemistry, University of Dhaka, Bangladesh. The authors also acknowledge the Department of Environment (DoE), Bangladesh, and the EAC4 (ECMWF Atmospheric Composition Reanalysis 4) global reanalysis dataset produced by the European Centre for Medium-Range Weather Forecasts (ECMWF) from Copernicus Atmosphere Monitoring Service (CAMS) for data support.