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Article

Chemical Composition of PM2.5 in Wood Fire and LPG Cookstove Homes of Nepali Brick Workers

by
James D. Johnston
1,*,
John D. Beard
1,
Emma J. Montague
1,
Seshananda Sanjel
2,
James H. Lu
1,
Haley McBride
1,
Frank X. Weber
3 and
Ryan T. Chartier
3
1
Department of Public Health, Brigham Young University, Provo, UT 84602, USA
2
Department of Community Medicine & Public Health, Karnali Academy of Health Sciences, Jumla 21200, Nepal
3
RTI International, Research Triangle Park, NC 27709, USA
*
Author to whom correspondence should be addressed.
Atmosphere 2021, 12(7), 911; https://doi.org/10.3390/atmos12070911
Submission received: 25 June 2021 / Revised: 11 July 2021 / Accepted: 12 July 2021 / Published: 15 July 2021
(This article belongs to the Special Issue Assessing Atmospheric Pollution and Its Impacts on the Human Health)
Versions Notes

Abstract

:
Household air pollution is a major cause of morbidity and mortality worldwide, largely due to particles ≤ 2.5 µm (PM2.5). The toxicity of PM2.5, however, depends on its physical properties and chemical composition. In this cross-sectional study, we compared the chemical composition of PM2.5 in brick workers’ homes (n = 16) based on use of wood cooking fire or liquefied petroleum gas (LPG) cookstoves. We collected samples using RTI International particulate matter (PM) exposure monitors (MicroPEMs). We analyzed filters for 33 elements using energy-dispersive X-ray fluorescence and, for black (BC) and brown carbon (BrC), integrating sphere optical transmittance. Wood fire homes had significantly higher concentrations of BC (349 µg/m3) than LPG homes (6.27 µg/m3, p < 0.0001) or outdoor air (5.36 µg/m3, p = 0.002). Indoor chlorine in wood fire homes averaged 5.86 µg/m3, which was approximately 34 times the average level in LPG homes (0.17 µg/m3, p = 0.0006). Similarly, potassium in wood fire homes (4.17 µg/m3) was approximately four times the level in LPG homes (0.98 µg/m3, p = 0.001). In all locations, we found aluminum, calcium, copper, iron, silicon, and titanium in concentrations exceeding those shown to cause respiratory effects in other studies. Our findings suggest the need for multi-faceted interventions to improve air quality for brick workers in Nepal.

1. Introduction

Household air pollution from the indoor burning of solid fuels, such as wood, crop residues, dung, or coal, is associated with 3.8 million deaths annually worldwide [1,2]. Exposure to household air pollution is associated with low birth weight, asthma, chronic obstructive pulmonary disease (COPD), respiratory infections, impaired immune function, coronary heart disease (CHD), stroke, cataracts, and cancers, including lung cancer [3,4,5,6]. Among household air pollutants generated from solid fuels, particulate matter (PM) less than or equal to 2.5 microns (µm) in aerodynamic diameter (PM2.5), also called fine particulate matter, may be the single largest contributor to this excess disease burden [7,8]. However, the toxicity of PM2.5 appears to be partially dependent on its chemical composition, which varies widely based on local emission sources [9,10,11,12,13,14,15,16].
In the Kathmandu Valley, Nepal, there are over 30,000 seasonal brick workers [17]. Most brick workers in Nepal live on-site at the brick kiln [18]. The most common type of housing for these workers is brick huts with tin roofs, often with poor ventilation to the outdoors [19]. Within this population of workers, the two primary methods of cooking are with indoor open wood fires or with liquefied petroleum gas (LPG) cookstoves [18,19]. Previous studies by our group found that Nepali brick workers, in addition to having hazardous work-related respiratory exposures [20], experience significant PM2.5 exposures during non-working hours [18,19]. Indoor PM2.5 concentrations in brick workers’ homes with wood fire and LPG cookstoves were 541.14 and 79.32 µg/m3, respectively, and these elevated levels coincided with meal and sleep times [19]. Brick workers suffer a disproportionate burden of respiratory symptoms compared to other workers in the same community [21], and we propose that these symptoms may be partially explained by elevated PM2.5 levels in brick workers’ homes, particularly among those cooking indoors with open wood fires.
PM2.5 generated during wood combustion is composed primarily of elemental (EC) and organic carbon (OC), nitrate and sulfate species, metals, and other elements [22]. However, wood smoke composition depends on the species of wood being burned and the burn temperature [22,23,24]. Low burn temperatures (300–500 °C), such as during the start-up phase of an open wood fire, generally produce larger particles composed of numerous OC species and low levels of trace elements and metals, while higher burn temperatures (>800 °C), such as during the burn phase of an open wood fire, produce smaller particles composed of higher EC/OC ratios, and higher levels of trace elements and metals [8,23].
The biological mechanisms behind many of the diseases associated with wood smoke inhalation are not well understood, but studies suggest some metals, metalloids, and nonmetal elements may play key roles in air pollution-related diseases [9]. For example, studies of PM2.5 constituents in ambient air pollution reported that the elements aluminum (Al), calcium (Ca), chlorine (Cl), iron (Fe), nickel (Ni), titanium (Ti), vanadium (V), and zinc (Zn), as well as black carbon (BC), are associated with increased hospitalizations and mortality, particularly among people ≥65 years of age [10,11]. The metals copper (Cu), Fe, potassium (K), and Zn, and the metalloid silicon (Si), are associated with respiratory hospital admissions in children, with the most serious effects seen in those ≤5 years of age [12]. The metals Al, Ni, Zn, V, and Ti, and the metalloid Si, are associated with low birth weight [13,14]. Several of these elements are present in wood smoke, in varying concentrations, depending on the species of wood and the burn temperature [22,24,25,26]. BC is associated with increased morbidity and mortality, primarily from heart and lung diseases [15]. Brown carbon (BrC), another constituent of PM2.5 found in areas where the use of solid biomass fuels is high [27], may also influence human health because it can attach to toxic chemicals, such as benzopyrene, and heavy metals [28].
Understanding the chemical composition of PM2.5 among specific populations may help elucidate relationships between exposure and disease. Our previous study measured the chemical composition of PM2.5 in brick workers’ homes during daytime hours when most home occupants were working, and thus did not capture pollutants generated during non-working hour activities such as cooking [18]. The purpose of this study, therefore, was to measure the chemical composition of PM2.5 over a full day in order to characterize non-working hour exposures.

2. Materials and Methods

2.1. Study Design

We collected PM2.5 samples using both filter-based and real-time nephelometer methods. Our previous study reported the PM2.5 total mass and nephelometer trend analyses [19]. For this study, we analyzed the 25 mm 3.0 µm PTFE filters (Zefon International, Ocala, FL, USA) for 35 chemical constituents. The methods for home selection, measures of housing characteristics, and air filter handling and sampling strategy, described briefly here, are described in full in our previously published paper [19]. We used a cross-sectional study design to measure PM2.5 constituents in brick workers’ homes (n = 17) from a single brick kiln in Bhaktapur, Nepal. We recruited homes by convenience sampling, and we classified them as either wood cooking fire or LPG cookstove homes. The typical construction of the homes sampled in this study was detailed previously [19]. We collected samples from 30 April to 3 May 2019 for approximately 21 h (median: 21.21; interquartile range: 2.21) in each home. We administered an extant questionnaire [18], by means of an interpreter, to measure housing factors, including number of people in the home, number of children in the home, primary fuel used for cooking, presence of smokers in the home, and the number of smokers in the home. We also measured the living area of the home and calculated the occupant density as the number of occupants divided by the home area in m2. Prior to data collection, Brigham Young University’s (BYU) Institutional Review Board (IRB) determined that this study did not meet the definition of human subject research, per 45 CFR 46 [29], based on the fact the unit of study was the home rather than the individual.

2.2. Indoor and Outdoor PM2.5 Measurements

We collected PM2.5 samples using MicroPEM V.3.2A personal exposure monitors (RTI International, Research Triangle Park, NC, USA), which we placed indoors, on a tripod, approximately 1.2 m from the floor. Simultaneous daily outdoor samples were collected on-site at the brick kiln in a centralized location. Detailed methods describing MicroPEM preparation, placement, and filter handling were described previously [19].

2.3. Elemental Analysis

RTI International performed the analysis of the 25 mm filters for 33 elements following the IO3.3 compendium method [30], which was modified for use with the Thermo (Thermo Fisher Scientific, Waltham, MA, USA) ARL energy-dispersive X-ray fluorescence instrument equipped with a silicon drift detector. This instrument configuration was used because it could produce enough spectral counts to fully quantify each element, while collimating the beam. The instrument was calibrated with thin-film standards (Micromatter Technologies Inc., Surrey, BC, Canada) that approximated PM deposition on a filter and the unknown samples were analyzed under identical excitation conditions. The samples were analyzed under vacuum with five different energy conditions to achieve maximum sensitivity, while avoiding overlapping spectra. A camera system within the instrument chamber was used to ensure the beam was focused on the exposed area of the filter to accurately quantify the elements of concern. A multi-element thin film standard was analyzed with each tray of samples to ensure there was acceptable instrument performance across the mass range and to assess instrument drift.

2.4. Carbon Analysis

Following gravimetric analysis, all sample filters were shipped to RTI International for optical analysis using RTI International’s integrating sphere optical transmittance technique [31]. The optical transmittance through the filter and the deposited PM sample were measured at seven wavelengths, ranging from near-infrared (940 nm) to blue (430 nm). All the sample filter transmittance data were adjusted using the mean transmittance of 10 blank filters from the same manufacturer’s lot. An empirically-derived algorithm used the measured wavelength-dependent transmittance values to quantify the BC and lightly absorbing BrC contributions to the total PM collected on the sample filter. This technique, and similar optical methods, have been used in numerous PM exposure studies as a low-cost and non-destructive means of obtaining basic PM compositional data from sample filters [32,33,34,35,36].

2.5. Statistical Analyses

All statistical analyses were conducted using SAS version 9.4 (SAS Institute, Inc., Cary, NC, USA). Although we collected 20 total PM2.5 samples, the filter of one sample tore and could not be analyzed for PM2.5 chemical components. Thus, we excluded that sample from all statistical analyses. We used α = 0.05 as the significance level for all analyses.
We calculated the frequencies and percentages for categorical characteristics of homes at the brick kiln and arithmetic means, standard deviations, minimums, first quartiles, medians, third quartiles, and maximums for the continuous characteristics of the homes at the brick kiln. For PM2.5 chemical components, we calculated the frequency and percentage of samples that had concentrations below the lower detection limits (LDL), at or between the LDLs and upper detection limits (UDL), and above the UDLs. We also calculated the geometric means (GM), 95% confidence intervals (CI), minimums, and maximums for concentrations of PM2.5 chemical components. We used GMs because the distributions of the concentrations of almost all PM2.5 chemical components were right-skewed. For individual PM2.5 chemical components that had all concentrations at or between the LDLs and UDLs, we used separate intercept-only linear regression models, with the natural logarithm of concentrations of individual PM2.5 chemical components as the dependent variables, and then exponentiated intercept coefficients to calculate GMs and 95% CIs. For individual PM2.5 chemical components with some concentrations below the LDLs or above the UDLs, we used separate intercept-only Tobit regression models, with the natural logarithm of concentrations of individual PM2.5 chemical components as the dependent variables, and then exponentiated intercept coefficients to calculate GMs and 95% CIs.
We used decision rules that were similar to those of Beard at al. [37], who based their decision rules on information from Lubin et al. [38], to determine the appropriate types of regression models to use for the analyses of individual PM2.5 chemical components with varying proportions of concentrations at or between the LDLs and UDLs. For the individual PM2.5 chemical components that had all concentrations at or between the LDLs and UDLs, we estimated the p-values and unadjusted associations between the individual characteristics of homes at the brick kiln and the concentrations of individual PM2.5 chemical components, using separate simple linear regression models, with the natural logarithm of the concentrations of individual PM2.5 chemical components as the dependent variables. For the individual PM2.5 chemical components that had >30–99% of concentrations at or between the LDLs and UDLs, we estimated the p-values and unadjusted associations between the individual characteristics of homes at the brick kiln and the concentrations of individual PM2.5 chemical components, using separate simple Tobit regression models, with the natural logarithm of the concentrations of individual PM2.5 chemical components as the dependent variables. For individual PM2.5 chemical components that had >0–30% of concentrations at or between the LDLs and UDLs, we estimated the p-values and unadjusted associations between individual characteristics of homes at the brick kiln and the concentrations of individual PM2.5 chemical components, using separate simple exact unconditional logistic regression models, with dichotomous indicator variables (i.e., one if the concentration was ≥LDL and zero if the concentration was <LDL) as dependent variables. For each of the three types of regression models, we exponentiated slope coefficients to calculate GMs, geometric mean ratios (GMR), or exact odds ratios (OR) and 95% CIs.
We considered several versions (e.g., linear; linear and quadratic; linear, quadratic, and cubic; natural logarithm; and categorical) of continuous characteristics of homes at the brick kilns and used the versions that had the lowest values of the Akaike Information Criterion (AIC) [39,40]. Where appropriate, we conducted pairwise comparisons of the GMs of concentrations of PM2.5 chemical components for each category of home area and fuel type and location and used the Tukey (linear regression models) or Tukey-Kramer (Tobit regression models) method to adjust the p-values for multiple comparisons. We estimated multivariable linear or Tobit regression models when more than one characteristic of homes at the brick kilns were statistically significantly associated with concentrations of a particular PM2.5 chemical component. For sensitivity analyses, we repeated analyses using home volume instead of home area.

3. Results

3.1. Characteristics of Homes of Brick Workers

For the 16 homes that we collected PM2.5 samples from (i.e., excluding the one home for which the filter tore), the home area was 5.41–9.50 m2 for 38%, >9.50–10.67 m2 for 31%, and >10.67–31.40 m2 for 31% (Table 1). The mean number of people in the home was 3.31 and the mean occupant density was 33.54 people per 100 m2. Sixty-three percent of homes had 0–1 children and 38% had 2–3 children. Fifty percent of homes had smokers and the median number of smokers in the home was 0.5. Sixty-nine percent of homes used LPG for fuel and 31% used wood.

3.2. Summary Statistics for PM2.5 Chemical Component Concentrations

Six PM2.5 chemical components had all concentrations below the LDLs (Table 2). For the other 29 PM2.5 chemical components, GMs of the concentrations ranged from 0.000042 μg/m3 for PM2.5 cerium to 16.09 μg/m3 for PM2.5 BC, with a median GM of 0.016 μg/m3 for PM2.5 barium (Ba).

3.3. Associations between Characteristics of Homes of Brick Workers and PM2.5 Chemical Component Concentrations

Home area was significantly associated with concentrations of PM2.5 Cl (p = 0.03) and PM2.5 Cu (p = 0.005; Supplementary Materials, Table S1). For PM2.5 Cl, pairwise comparisons indicated significant differences between 5.41–9.50 m2 (GM = 2.95 μg/m3) and >10.67–31.40 m2 (GM = 0.14 μg/m3; p = 0.04), but not between 5.41–9.50 m2 and >9.50–10.67 m2 (GM = 0.25 μg/m3; p = 0.10) or >9.50–10.67 m2 and >10.67–31.40 m2 (p = 0.85). For PM2.5 Cu, pairwise comparisons indicated significant differences between 5.41–9.50 m2 (GM = 0.013 μg/m3) and >9.50–10.67 m2 (GM = 0.0024 μg/m3; p = 0.01), and between 5.41–9.50 m2 and >10.67–31.40 m2 (GM = 0.0035 μg/m3; p = 0.03), but not between >9.50–10.67 m2 and >10.67–31.40 m2 (p = 0.82). The number of people in the home, occupant density, and the number of children in the home were not significantly associated with concentrations of any PM2.5 chemical component (Supplementary Materials, Tables S1 and S2). The presence of smokers in the home was significantly associated with concentrations of 22 of 29 (76%) PM2.5 chemical components, and the GMs of concentrations were higher in homes with smokers than in homes without smokers for all 22 significant associations (Table 3). Similarly, the number of smokers in the home was significantly associated with concentrations of 20 (69%) PM2.5 chemical components and the GMRs were greater than one for all 20 significant associations (i.e., the GMs of the concentrations of those 20 PM2.5 chemical components increased as the number of smokers in the home increased). Fuel type and location was significantly associated with concentrations of 22 (76%) PM2.5 chemical components (Table 4). Pairwise comparisons indicated significant differences between LPG, indoor, and wood, indoor, for 21 (95%) of the significant associations, and the GMs of concentrations were higher for wood, indoor, than for LPG, indoor, for all 21 significant differences. Pairwise comparisons indicated significant differences between LPG, indoor, and outdoor for one (5%) of the significant associations (i.e., PM2.5 BrC) and the GM of concentrations was higher for LPG, indoor, than for outdoor. Pairwise comparisons indicated a significant difference between wood, indoor, and outdoor for six (27%) of the significant associations, and the GMs of concentrations were higher for wood, indoor, than for outdoor for all six significant differences.

3.4. Adjusted Associations between Characteristics of Homes of Brick Workers and PM2.5 Chemical Component Concentrations

Smokers in the home was most consistently significantly associated with PM2.5 Cl and PM2.5 Cu when some combination of home area, smokers in the home or number of smokers in the home, and fuel type were included as independent variables in the multivariable linear regression models (Supplementary Materials, Table S3). Smokers in the home was significantly associated with concentrations of six (24%) PM2.5 chemical components, and fuel type was significantly associated with concentrations of nine (36%) PM2.5 chemical components when smokers in the home and fuel type were included as independent variables in the multivariable linear or Tobit regression models (Table 5). The number of smokers in the home was not significantly associated with concentrations of any PM2.5 chemical component, but fuel type was significantly associated with concentrations of 14 (56%) PM2.5 chemical components when the number of smokers in the home and fuel type were included as independent variables in the multivariable linear or Tobit regression models (Table 6).

3.5. Sensitivity Analyses

The results were almost identical when we repeated analyses using home volume instead of home area (not shown), with the one exception being that home volume was not significantly associated with concentrations of PM2.5 Cl (8.52–16.00 m3: GM = 1.23; 95% CI: 0.26, 5.94 μg/m3; and >16.00–53.44 m3: GM = 0.22; 95% CI: 0.046, 1.06 μg/m3; p = 0.12). In other words, home volume was significantly associated with concentrations of PM2.5 Cu (8.52–16.00 m3: GM = 0.0086; 95% CI: 0.0043, 0.017 μg/m3; and >16.00–53.44 m3: GM = 0.0030; 95% CI: 0.0014, 0.0063 μg/m3; p = 0.04), but not with concentrations of any other PM2.5 chemical component (not shown).

4. Discussion

This research was conducted as a follow-up to a previous study we conducted in 2018 [18]. In our previous study, we collected PM2.5 samples in on-site brick workers’ homes in Bhaktapur, Nepal, but the sampling time was limited to approximately seven hours during the middle of the day when most workers were not at home. Thus, we were not able to measure PM2.5 generated during cooking and other household activities during non-working hours. The longer sampling time (approximately 21 h in each home) used in the current study allowed us to characterize PM2.5 constituents across both working and non-working hours. Using the seven-hour samples in our previous study, we found no difference in the chemical composition of indoor vs. outdoor air, except for Cl, which was higher indoors. Our previous study also found that the primary fuel used for cooking was significantly associated with only two PM2.5 chemical components, Cl and K, which were both higher in wood fuel homes. In contrast, in this study we found significant differences for 22 chemical components based on cooking fuel type and location (LPG, indoor vs. wood, indoor vs. outdoor). Pairwise comparisons indicated fuel type was the primary source of these significant differences. We attributed these differences in results among studies to non-working hour activities in the home that were not captured in our previous study, but were captured in our current study.
The major elemental aerosol-phase tracers of wood smoke are Cl and K, both of which are commonly found in PM2.5 generated from wood combustion [41]. Like our previous study, we found significantly higher levels of both elements in homes where wood fires were used for cooking. For wood fire homes, the indoor Cl level averaged 5.86 µg/m3, which was approximately 34 times the average level in LPG homes (0.17 µg/m3). Similarly, K levels in wood fire homes (4.17 µg/m3) were approximately four times the levels in LPG homes (0.98 µg/m3). Furthermore, our results showed significant differences in Cl and K levels between wood fire homes and outdoor air, but not between LPG homes and outdoor air, suggesting the high levels of Cl and K in our study originated from cooking indoors over wood fires. Our findings are consistent with previous studies conducted in homes in West Africa and India. In higher-income homes in Accra, Ghana, where residents tend to cook indoors with LPG cookstoves, Zhou et al. reported average indoor Cl and K levels of 0.34 and 1.08 µg/m3, respectively [42]. By comparison, average Cl and K levels in enclosed cookhouses using firewood in The Gambia were 7.90 and 10.75 µg/m3, respectively [42]. In unventilated, low-income homes in India where solid biomass fuels were used for cooking, annual Cl and K levels averaged 5.8 and 7.6 µg/m3, respectively [43].
Among the 35 analytes, BC accounted for the highest concentration in wood fire homes (349.04 µg/m3), where levels were 56 and 65 times the levels in LPG homes and outdoor air, respectively. BC is released into the air as a result of incomplete combustion of fuels, and prolonged or extreme exposure is associated with increased morbidity and mortality, primarily from cardiac and respiratory illnesses [15]. When BC acts as a carrier for polycyclic aromatic hydrocarbons, it is linked to adverse health effects, including cancer and severe immune, reproductive, and pulmonary damage [15,44]. Several additional elemental species identified in our study were previously shown to be associated with burning wood. For example, we found concentrations of Al, Ca, magnesium (Mg), phosphorus (P), and Si were significantly higher in homes with wood cooking fires than in homes with LPG cookstoves. All of these elements were shown in previous studies to be associated with high temperature burning of wood or wood pellets in stoves [23,45].
Respiratory illnesses are common among brick workers in Nepal [21], and occupational exposures likely play an important role in this finding [20]. However, previous studies of urban ambient PM2.5 constituents found that several metals and other elements were associated with respiratory disease in adults and children [10,12] at much lower concentrations than those found in our study. For example, Bell et al. found associations between respiratory hospital admissions in adults ≥65 years of age and PM2.5 constituents Al, Ca, Cl, BC, Ni, Si, Ti, and V [10]. In our study, all of these constituents, with the exception of Ni and V, were found in higher concentrations than those reported by Bell et al. in all sampled locations (wood indoor, LPG indoor, and outdoor air), and V concentrations in our study were higher in wood fire homes. Ostro et al. found associations between respiratory hospital admissions in children and concentrations of Cu, Fe, K, Si, and Zn in ambient air [12]. Again, we found each of these constituents in our samples, and in most cases at higher concentrations than those reported by Ostro et al. Differences in concentrations were most pronounced in wood fire homes, where element concentrations ranged from 1.9–35 times the ambient concentrations reported by Ostro et al. We propose that repeated exposure to the high concentrations of metals and other elements in both indoor and outdoor air may contribute significantly to the respiratory symptoms seen among brick workers in Nepal.
One of the most noticeable differences between this study and our previous one was the number of chemical components that had significantly higher concentrations in homes with smokers. Depending on the tobacco source, cigarette smoke contains varying levels of several metals that are associated with deleterious health effects, including Al, arsenic (As), Ba, beryllium (Be), cadmium (Cd), cobalt (Co), chromium (Cr), Cu, Fe, lead (Pb), manganese (Mn), mercury (Hg), Ni, selenium (Se), Si, V, and Zn [46,47]. Our current study found these metals in higher concentrations in homes with smokers compared to homes with non-smokers, with the exception of Cd, which had all sample concentrations below the LDL, and Be and Hg, which we did not test for. Toxicologically, these metals are associated with allergic sensitization and inflammation, COPD, cancer, asthma, immune system suppression [47], vascular endothelium damage, and the development of atherosclerosis [46].
In our previous study, we discussed concerns about small, overcrowded housing among brick workers in Nepal, and specifically regarding the potential for indoor pollution to concentrate in smaller, poorly ventilated homes [18]. The finding that home area was significantly associated with PM2.5 Cl and Cu appears to support this concern. In the cases of both Cl and Cu, smaller homes (i.e., 5.41–9.50 m2) had the highest concentrations (Supplementary Materials, Table S1). Although not statistically significant, smaller homes also had the highest GM concentrations for 22 other chemical components. Smaller home area appears to contribute to a build-up in air pollution concentrations. The small sample size and reduced statistical power in this study may have contributed to our inability to detect significant associations between home area and concentrations of PM2.5 constituents for elements other than Cl and Cu.
We used multivariable linear or Tobit regression models that included two or three characteristics of homes at the brick kilns (i.e., smoking, fuel type, and home area) as independent variables to determine whether significant associations between these characteristics and concentrations of PM2.5 chemical components, found using simple (unadjusted) regression models, remained statistically significant when we adjusted for the other characteristic(s). As stated previously, Cu, Ni, and Se were previously found in cigarette smoke [46,47] and all three PM2.5 chemical components were significantly associated with smokers in the home in our study when we adjusted for fuel type. In addition, Cu was significantly associated with smokers in the home when we adjusted for home area and fuel type. Al, BC, Cl, Mg, P, and K were previously found in wood smoke [15,23,41,45] and all six PM2.5 chemical components were significantly associated with fuel type in our study when we adjusted for smokers in the home and/or number of smokers in the home. However, Cl was not significantly associated with fuel type when we adjusted for home area and smokers in the home or number of smokers in the home. Cl was instead significantly associated with smokers in the home when we adjusted for home area and fuel type. Ba, Pb, Mn, V, and Zn were previously found in cigarette smoke [46,47], but none of these PM2.5 chemical components were significantly associated with smokers in the home or number of smokers in the home in our study when we adjusted for fuel type. All five PM2.5 chemical components were instead significantly associated with fuel type when we adjusted for smokers in the home and/or number of smokers in the home. The reasons for these discrepancies between our results and those of previous studies are unknown, but our small sample size and the fact that all five homes that used wood for fuel also had smokers in the home may have contributed.
Although we did not have a sufficient sample size to conduct principal component analysis in this study, we can make some conjecture about possible pollution sources. Of the 29 analytes that had at least one sample concentration above the LDL, only one (BrC) was significantly different between LPG homes and outdoor air. This finding may be explained by stir-fry cooking within the home [48], or possibly by activities such as burning candles or smoking indoors during non-working hours. Non-significant differences in the remaining 28 analytes may be largely explained by infiltration of ambient air pollution through gaps in brick workers’ homes, as discussed previously [18,19]. There are currently over 100 operating brick kilns in the Kathmandu Valley, most of which are coal fired [17,49,50]. Several analytes from our samples are known to originate from coal burning, such as Al, As, Ba, Ca, Fe, K, Mg, Mn, P, Se, Si, and Ti, depending on the source of the coal [51]. In addition, the kiln from which our samples were collected is located near the Araniko Highway, a major roadway through Bhaktapur. Vehicle exhaust is a source of several metals that we found in ambient air, as well as in participant homes, including Cr, Cu, Fe, Ni, Pb, and Zn [52,53,54]. Tire fading and brake wear may be responsible for Zn and Cd, and Cu and Zn, respectively [52,55], although Cd concentrations were below the LDL for all samples in our study.
One limitation in understanding the contribution of wood burning to elemental composition in our study is that we did not measure burn temperature, which greatly affects the chemical composition of particles [24]. In future studies, we may also consider using the EC/OC ratio or measuring methyl chloride levels as more definitive markers of wood smoke in our study homes, as well as looking more closely at the bioavailability of PM-bound metals to understand the toxicological properties of PM2.5 in brick workers’ homes. We were unable to obtain measurements for BrC for four samples because the amount of BC on the filters surpassed the UDL, which rendered the optical transmittance method unfeasible. This study was also limited because samples were obtained from homes at a single brick kiln and we had a relatively small sample size. A larger sample size would have allowed for the use of principal component analysis or related methods, such as positive matrix factorization, which was used in other studies [42], to determine the sources of pollution. Other limitations of this study (e.g., unmeasured confounding by temporal factors, lack of health data, etc.) were discussed previously [19].

5. Conclusions

Based on the findings of this and other studies [18,19], we suggest a multi-faceted approach is needed to protect brick workers in the Kathmandu Valley from the adverse health effects associated with poor air quality. The atmospheric pressure, wind direction and velocity, humidity, and the bowl-shaped topography of Kathmandu Valley add to the air pollution problems [56]. As air pollution remains a major issue, it is of paramount importance to educate the general population regarding the detrimental effects of air pollution and preventative measures to inhibit extreme outcomes [57]. The government of Nepal has to take primary responsibility to address the consequences of this problem by developing policies and action plans to reduce ambient air pollution and, ultimately, its consequences [57]. As the primary source of indoor air pollution in Nepal is the burning of solid fuels for cooking, improved stoves, smoke hoods, vented or chimney stoves, and clean fuel replacements would reduce the disease burden due to indoor air pollution exposure [58]. Considering 50% of homes in this study had at least one smoker, and that smoking is a significant predictor of respiratory illness among brick workers in Nepal [21], future interventions to improve indoor air quality in brick workers’ homes should also include smoking cessation programs [59,60].

Supplementary Materials

The following are available online at https://www.mdpi.com/article/10.3390/atmos12070911/s1, Table S1: Associations between the mean of samples inside homes and home area and number of people in home at a brick kiln in Bhaktapur, Nepal, May 2019, Table S2: Associations between the mean of samples inside homes and occupant density and number of children in home at a brick kiln in Bhaktapur, Nepal, May 2019, and Table S3: Associations between the mean of samples inside homes and home area, smokers in home, number of smokers in home, and fuel type mutually adjusted for each other at a brick kiln in Bhaktapur, Nepal, May 2019.

Author Contributions

Conceptualization, J.D.J., J.D.B., F.X.W. and R.T.C.; methodology, J.D.J., J.D.B., F.X.W. and R.T.C.; validation, F.X.W. and R.T.C.; formal analysis, J.D.B., F.X.W., R.T.C. and J.D.J.; investigation, J.D.J.; resources, J.D.J., F.X.W. and R.T.C.; data curation, J.D.J., J.D.B., F.X.W. and R.T.C.; writing—original draft preparation, J.D.J., J.D.B., E.J.M., S.S., J.H.L., H.M., F.X.W. and R.T.C.; writing—review and editing, J.D.J., J.D.B., E.J.M., S.S., J.H.L., H.M., F.X.W. and R.T.C.; supervision, J.D.J. and J.D.B.; project administration, J.D.J. All authors have read and agreed to the published version of the manuscript.

Funding

This research received no external funding.

Institutional Review Board Statement

Brigham Young University’s (BYU) Institutional Review Board (IRB) determined this study did not meet the definition of human subject research, per 45 CFR 46 [29], based on the fact that the unit of study was the home rather than the individual.

Informed Consent Statement

Not Applicable.

Data Availability Statement

The data presented in this study are available upon request from the corresponding author.

Acknowledgments

We thank the brick kiln manager and staff, Sirish, our interpreter, and especially the brick workers and their families for providing support during sample collection.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. World Health Organization. Household Air Pollution and Health. 2018. Available online: https://www.who.int/news-room/fact-sheets/detail/household-air-pollution-and-health (accessed on 21 May 2021).
  2. Landrigan, P.J.; Fuller, R.; Acosta, N.J.R.; Adeyi, O.; Arnold, R.; Basu, N.; Baldé, A.B.; Bertollini, R.; Bose-O’Reilly, S.; Boufford, J.I.; et al. The Lancet Commission on pollution and health. Lancet 2018, 391, 462–512. [Google Scholar] [CrossRef] [Green Version]
  3. Fullerton, D.G.; Bruce, N.; Gordon, S. Indoor air pollution from biomass fuel smoke is a major health concern in the developing world. Trans. R. Soc. Trop. Med. Hyg. 2008, 102, 843–851. [Google Scholar] [CrossRef] [Green Version]
  4. Kim, K.-H.; Jahan, S.A.; Kabir, E. A review of diseases associated with household air pollution due to the use of biomass fuels. J. Hazard. Mater. 2011, 192, 425–431. [Google Scholar] [CrossRef]
  5. Zhang, J.; Smith, K.R. Household Air Pollution from Coal and Biomass Fuels in China: Measurements, Health Impacts, and Interventions. Environ. Health Perspect. 2007, 115, 848–855. [Google Scholar] [CrossRef]
  6. Apte, K.; Salvi, S. Household air pollution and its effects on health. F1000Research 2016, 5, 2593. [Google Scholar] [CrossRef]
  7. Mannucci, P.M.; Harari, S.; Martinelli, I.; Franchini, M. Effects on health of air pollution: A narrative review. Intern. Emerg. Med. 2015, 10, 657–662. [Google Scholar] [CrossRef]
  8. GBD 2013 Risk Factors Collaborators; Forouzanfar, M.H.; Alexander, L.; Anderson, H.R.; Bachman, V.F.; Biryukov, S.; Brauer, M.; Burnett, R.; Casey, D.; Coates, M.M.; et al. Global, regional, and national comparative risk assessment of 79 behavioural, environmental and occupational, and metabolic risks or clusters of risks in 188 countries, 1990–2013: A systematic analysis for the Global Burden of Disease Study 2013. Lancet 2015, 386, 2287–2323. [Google Scholar] [CrossRef] [Green Version]
  9. Schwarze, P.E.; Øvrevik, J.; Låg, M.; Refsnes, M.; Nafstad, P.; Hetland, R.B.; Dybing, E. Particulate matter properties and health effects: Consistency of epidemiological and toxicological studies. Hum. Exp. Toxicol. 2006, 25, 559–579. [Google Scholar] [CrossRef] [PubMed]
  10. Bell, M.L.; Ebisu, K.; Leaderer, B.; Gent, J.F.; Lee, H.J.; Koutrakis, P.; Wang, Y.; Dominici, F.; Peng, R.D. Associations of PM2.5 Constituents and Sources with Hospital Admissions: Analysis of Four Counties in Connecticut and Massachusetts (USA) for Persons ≥65 Years of Age. Environ. Health Perspect. 2014, 122, 138–144. [Google Scholar] [CrossRef] [Green Version]
  11. Burnett, R.T.; Book, J.; Dann, T.; Delocla, C.; Philips, O.; Cakmak, S.; Vincent, R.; Goldberg, M.S.; Krewski, D. Association between particulate- and gas-phase components of urban air pollution and daily mortality in eight Canadian cities. Inhal. Toxicol. 2000, 12, 15–39. [Google Scholar] [CrossRef] [PubMed]
  12. Ostro, B.; Roth, L.; Malig, B.; Marty, M. The Effects of Fine Particle Components on Respiratory Hospital Admissions in Children. Environ. Health Perspect. 2009, 117, 475–480. [Google Scholar] [CrossRef] [Green Version]
  13. Ebisu, K.; Bell, M. Airborne PM 2.5 Chemical Components and Low Birth Weight in the Northeastern and Mid-Atlantic Regions of the United States. Environ. Health Perspect. 2012, 120, 1746–1752. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  14. Bell, M.L.; Belanger, K.; Ebisu, K.; Gent, J.F.; Lee, H.J.; Koutrakis, P.; Leaderer, B.P. Prenatal exposure to fine particulate matter and birth weight: Variations by particulate constituents and sources. Epidemiology 2010, 21, 884. [Google Scholar] [CrossRef] [Green Version]
  15. Ali, M.U.; Siyi, L.; Yousaf, B.; Abbas, Q.; Hameed, R.; Zheng, C.; Kuang, X.; Wong, M.H. Emission sources and full spectrum of health impacts of black carbon associated polycyclic aromatic hydrocarbons (PAHs) in urban environment: A review. Crit. Rev. Environ. Sci. Technol. 2021, 51, 857–896. [Google Scholar] [CrossRef]
  16. Laden, F.; Neas, L.M.; Dockery, D.W.; Schwartz, J. Association of fine particulate matter from different sources with daily mortality in six U.S. cities. Environ. Health Perspect. 2000, 108, 941–947. [Google Scholar] [CrossRef] [PubMed]
  17. Haack, B.N.; Khatiwada, G. Rice and Bricks: Environmental Issues and Mapping of the Unusual Crop Rotation Pattern in the Kathmandu Valley, Nepal. Environ. Manag. 2007, 39, 774–782. [Google Scholar] [CrossRef]
  18. Thygerson, S.M.; Beard, J.D.; House, M.J.; Smith, R.L.; Burbidge, H.C.; Andrus, K.N.; Weber, F.; Chartier, R.; Johnston, J.D. Air-Quality Assessment of On-Site Brick-Kiln Worker Housing in Bhaktapur, Nepal: Chemical Speciation of Indoor and Outdoor PM2.5 Pollution. Int. J. Environ. Res. Public Health 2019, 16, 4114. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  19. Johnston, J.D.; Hawks, M.E.; Johnston, H.B.; Johnson, L.A.; Beard, J.D. Comparison of Liquefied Petroleum Gas Cookstoves and Wood Cooking Fires on PM2.5 Trends in Brick Workers’ Homes in Nepal. Int. J. Environ. Res. Public Health 2020, 17, 5681. [Google Scholar] [CrossRef]
  20. Sanjel, S.; Khanal, S.N.; Thygerson, S.M.; Carter, W.; Johnston, J.D.; Joshi, S.K. Exposure to respirable silica among clay brick workers in Kathmandu valley, Nepal. Arch. Environ. Occup. Health 2018, 73, 347–350. [Google Scholar] [CrossRef]
  21. Sanjel, S.; Khanal, S.N.; Thygerson, S.M.; Carter, W.S.; Johnston, J.D.; Joshi, S.K. Respiratory symptoms and illnesses related to the concentration of airborne particulate matter among brick kiln workers in Kathmandu valley, Nepal. Ann. Occup. Environ. Med. 2017, 29, 9. [Google Scholar] [CrossRef] [Green Version]
  22. Fine, P.M.; Cass, G.R.; Simoneit, B.R. Chemical characterization of fine particle emissions from fireplace combustion of woods grown in the northeastern United States. Environ. Sci. Technol. 2001, 35, 2665–2675. [Google Scholar] [CrossRef]
  23. Bolling, A.K.; Pagels, J.; Yttri, K.E.; Barregard, L.; Sallsten, G.; Schwarze, P.E.; Boman, C. Health effects of residential wood smoke particles: The importance of combustion conditions and physicochemical particle properties. Part. Fibre Toxicol. 2009, 6, 29. [Google Scholar] [CrossRef] [Green Version]
  24. Rau, J.A. Composition and Size Distribution of Residential Wood Smoke Particles. Aerosol Sci. Technol. 1989, 10, 181–192. [Google Scholar] [CrossRef] [Green Version]
  25. Kleeman, M.J.; Schauer, A.J.J.; Cass, G.R. Size and Composition Distribution of Fine Particulate Matter Emitted from Wood Burning, Meat Charbroiling, and Cigarettes. Environ. Sci. Technol. 1999, 33, 3516–3523. [Google Scholar] [CrossRef]
  26. Larson, T.V.; Koenig, J.Q. Wood smoke: Emissions and noncancer respiratory effects. Ann. Rev. Public Health 1994, 15, 133–156. [Google Scholar] [CrossRef]
  27. Laskin, A.; Laskin, J.; Nizkorodov, S. Chemistry of Atmospheric Brown Carbon. Chem. Rev. 2015, 115, 4335–4382. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  28. Yan, J.; Wang, X.; Gong, P.; Wang, C.; Cong, Z. Review of brown carbon aerosols: Recent progress and perspectives. Sci. Total Environ. 2018, 634, 1475–1485. [Google Scholar] [CrossRef] [PubMed]
  29. US Department of Health and Human Services. Code of Federal Regulations, Title 45, Part 46, Protection of Human Subjects, Part 46.102. Available online: https://www.hhs.gov/ohrp/regulations-and-policy/regulations/45-cfr-46/revised-common-rule-regulatory-text/index.html (accessed on 13 July 2021).
  30. Kellog, B.; Winberry, W.T. Determination of metals in ambient particulate matter using x-ray fluorescence (XRF) spectroscopy. In Compendium of Methods for the Determination of Inorganic Compounds in Ambient Air; US EPA: Cincinatti, OH, USA, 1999. [Google Scholar]
  31. Lawless, P.A.; Rodes, C.E.; Ensor, D.S. Multiwavelength absorbance of filter deposits for determination of environmental tobacco smoke and black carbon. Atmos. Environ. 2004, 38, 3373–3383. [Google Scholar] [CrossRef]
  32. Williams, R.; Rea, A.; Vette, A.; Croghan, C.; Whitaker, D.; Stevens, C.; McDow, S.; Fortmann, R.; Sheldon, L.; Wilson, H.; et al. The design and field implementation of the Detroit Exposure and Aerosol Research Study. J. Expo. Sci. Environ. Epidemiol. 2008, 19, 643–659. [Google Scholar] [CrossRef]
  33. Rodes, C.E.; Lawless, P.A.; Thornburg, J.; Williams, R.W.; Croghan, C.W. DEARS particulate matter relationships for personal, indoor, outdoor, and central site settings for a general population. Atmos. Environ. 2010, 44, 1386–1399. [Google Scholar] [CrossRef]
  34. Zhao, W.; Hopke, P.K.; Gelfand, E.W.; Rabinovitch, N. Use of an expanded receptor model for personal exposure analysis in schoolchildren with asthma. Atmos. Environ. 2007, 41, 4084–4096. [Google Scholar] [CrossRef]
  35. Williams, R.; Jones, P.; Croghan, C.; Thornburg, J.; Rodes, C. The influence of human and environmental exposure factors on personal NO2 exposures. J. Expo. Sci. Environ. Epidemiol. 2011, 22, 109–115. [Google Scholar] [CrossRef] [Green Version]
  36. Sloan, C.D.; Weber, F.; Bradshaw, R.K.; Philipp, T.J.; Barber, W.B.; Palmer, V.L.; Graul, R.J.; Tuttle, S.C.; Chartier, R.T.; Johnston, J.D. Elemental analysis of infant airborne particulate exposures. J. Expo. Sci. Environ. Epidemiol. 2016, 27, 526–534. [Google Scholar] [CrossRef]
  37. Beard, J.D.; Erdely, A.; Dahm, M.M.; de Perio, M.A.; Birch, M.E.; Evans, D.E.; Fernback, J.E.; Eye, T.; Kodali, V.; Mercer, R.R.; et al. Carbon nanotube and nanofiber exposure and sputum and blood biomarkers of early effect among U.S. workers. Environ. Int. 2018, 116, 214–228. [Google Scholar] [CrossRef]
  38. Lubin, J.H.; Colt, J.S.; Camann, D.; Davis, S.; Cerhan, J.; Severson, R.K.; Bernstein, L.; Hartge, P. Epidemiologic Evaluation of Measurement Data in the Presence of Detection Limits. Environ. Health Perspect. 2004, 112, 1691–1696. [Google Scholar] [CrossRef]
  39. Akaike, H. A new look at the statistical model identification. IEEE Trans. Autom. Control. 1974, 19, 716–723. [Google Scholar] [CrossRef]
  40. Howe, C.J.; Cole, S.R.; Westreich, D.; Greenland, S.; Napravnik, S.; Eron, J.J. Splines for Trend Analysis and Continuous Confounder Control. Epidemiology 2011, 22, 874–875. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  41. Khalil, M.; Rasmussen, R. Tracers of wood smoke. Atmospheric Environ. 2003, 37, 1211–1222. [Google Scholar] [CrossRef]
  42. Zhou, Z.; Dionisio, K.L.; Verissimo, T.G.; Kerr, A.S.; Coull, B.; Howie, S.; Arku, R.E.; Koutrakis, P.; Spengler, J.D.; Fornace, K.; et al. Chemical Characterization and Source Apportionment of Household Fine Particulate Matter in Rural, Peri-urban, and Urban West Africa. Environ. Sci. Technol. 2014, 48, 1343–1351. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  43. Matawle, J.L.; Pervez, S.; Shrivastava, A.; Tiwari, S.; Pant, P.; Deb, M.K.; Bisht, D.S.; Pervez, Y.F. PM2.5 pollution from household solid fuel burning practices in central India: 1. Impact on indoor air quality and associated health risks. Environ. Geochem. Health 2017, 39, 1045–1058. [Google Scholar] [CrossRef] [PubMed]
  44. Breton, C.V.; Marutani, A.N. Air Pollution and Epigenetics: Recent Findings. Curr. Environ. Health Rep. 2014, 1, 35–45. [Google Scholar] [CrossRef] [Green Version]
  45. Lind, T.; Vaimari, T.; Kauppinen, E.; Nilsson, K.; Sfiris, G.; Maenhaut, W. ASH formation mechanisms during combustion of wood in circulating fluidized beds. Proc. Combust. Inst. 2000, 28, 2287–2295. [Google Scholar] [CrossRef]
  46. Bernhard, D.; Rossmann, A.; Wick, G. Metals in cigarette smoke. IUBMB Life 2005, 57, 805–809. [Google Scholar] [CrossRef]
  47. Pappas, R.S. Toxic elements in tobacco and in cigarette smoke: Inflammation and sensitization. Metallomics 2011, 3, 1181–1198. [Google Scholar] [CrossRef] [Green Version]
  48. Sankhyan, S. Indoor black and brown carbon from cooking activities and outdoor penetration: Insights from the HOMEChem Study. Ph.D. Thesis, University of Colorado at Boulder, Boulder, CO, USA, 2019. [Google Scholar]
  49. ENPHO. A Study on Status of Brick Industry in the Kathmandu Valley; ENPHO: Kathmandu, Nepal, 2001. [Google Scholar]
  50. Raut, A. Brick Kilns in Kathmandu Valley: Current status, environmental impacts and future options. Himal. J. Sci. 2003, 1, 59–61. [Google Scholar] [CrossRef] [Green Version]
  51. Watson, J.G.; Chow, J.C.; E Houck, J. PM2.5 chemical source profiles for vehicle exhaust, vegetative burning, geological material, and coal burning in Northwestern Colorado during 1995. Chemosphere 2001, 43, 1141–1151. [Google Scholar] [CrossRef]
  52. Hong, N.; Zhu, P.; Liu, A.; Zhao, X.; Guan, Y. Using an innovative flag element ratio approach to tracking potential sources of heavy metals on urban road surfaces. Environ. Pollut. 2018, 243, 410–417. [Google Scholar] [CrossRef] [PubMed]
  53. Kumari, S.; Jain, M.K.; Elumalai, S.P. Assessment of Pollution and Health Risks of Heavy Metals in Particulate Matter and Road Dust Along the Road Network of Dhanbad, India. J. Health Pollut. 2021, 11, 210305. [Google Scholar]
  54. Bilos, C.; Colombo, J.C.; Skorupka, C.N.; Presa, M.J.R. Sources, distribution and variability of airborne trace metals in La Plata City area, Argentina. Environ. Pollut. 2001, 111, 149–158. [Google Scholar] [CrossRef]
  55. Hjortenkrans, D.S.T.; Bergbäck, B.G.; Häggerud, A.V. Metal Emissions from Brake Linings and Tires: Case Studies of Stockholm, Sweden 1995/1998 and 2005. Environ. Sci. Technol. 2007, 41, 5224–5230. [Google Scholar] [CrossRef] [PubMed]
  56. Giri, D.; Krishna, M.V.; Adhikary, P.R. The influence of meteorological conditions on PM10 concentrations in Kathmandu Valley. Int. J. Environ. Res. 2008, 2, 49–60. [Google Scholar]
  57. SSaud, B.; Paudel, G. The Threat of Ambient Air Pollution in Kathmandu, Nepal. J. Environ. Public Health 2018, 2018, 1504591. [Google Scholar] [CrossRef] [Green Version]
  58. Malla, M.B.; Bruce, N.; Bates, E.; Rehfuess, E. Applying global cost-benefit analysis methods to indoor air pollution mitigation interventions in Nepal, Kenya and Sudan: Insights and challenges. Energy Policy 2011, 39, 7518–7529. [Google Scholar] [CrossRef]
  59. Van den Brand, F.; Anagelhout, G.; Winkens, B.; Chavannes, N.H.; Van Schayck, O.C.P. Effect of a workplace-based group training programme combined with financial incentives on smoking cessation: A cluster-randomised controlled trial. Lancet Public Health 2018, 3, e536–e544. [Google Scholar] [CrossRef] [Green Version]
  60. Cahill, K.; Lancaster, T.R. Workplace interventions for smoking cessation. Cochrane Database Syst. Rev. 2014. [Google Scholar] [CrossRef] [PubMed]
Table
Table 1. Characteristics of homes a at a brick kiln in Bhaktapur, Nepal (May 2019).
Table 1. Characteristics of homes a at a brick kiln in Bhaktapur, Nepal (May 2019).
CharacteristicHomes, n (%)MeanSDMinQ1MedianQ3Max
Total16 (100)
Home area b, m2
5.41–9.506 (38)
>9.50–10.675 (31)
>10.67–31.405 (31)
Number of people in home 3.311.541.002.003.004.007.00
Occupant density, number of people/100 m2 33.5417.009.5522.4730.1138.5573.96
Number of children in home
0–110 (63)
2–36 (38)
Smokers in home
No8 (50)
Yes8 (50)
Number of smokers in home 0.751.060.000.000.501.004.00
Fuel type
LPG11 (69)
Wood5 (31)
Abbreviations: LPG, liquefied petroleum gas; Max, maximum; Min, minimum; Q1, first quartile; Q3, third quartile; and SD, standard deviation. a The filter of one sample tore and could not be analyzed, and, thus, was excluded from analyses. b Categories based on tertiles.
Table
Table 2. Summary statistics for the mean of samples inside or outside homes a at a brick kiln in Bhaktapur, Nepal (May 2019).
Table 2. Summary statistics for the mean of samples inside or outside homes a at a brick kiln in Bhaktapur, Nepal (May 2019).
Between LDL and UDL
PM2.5 Chemical
Component, μg/m3		LDL Mass (μg)LDL Concentration RangeMissing, nBelow LDL, n (%)n (%)GM b95% CI bMin cMax cAbove UDL
Al0.0120.018, 0.052 2 (11)17 (89)0.300.14, 0.660.0312.190 (0)
Sb0.240.34, 1.01 19 (100)0 (0)NANANANA0 (0)
As0.00240.0034, 0.010 17 (89)2 (11)0.00310.0025, 0.00390.00390.00390 (0)
Ba0.00470.0068, 0.020 7 (37)12 (63)0.0160.0083, 0.0320.0100.100 (0)
BC0.500.73, 2.15 1 (5)14 (74)16.095.82, 44.521.84107.364 (21) d
Br0.00210.0030, 0.0089 0 (0)19 (100)0.022 e0.016, 0.030 e0.00780.0610 (0)
BrC0.500.73, 2.1540 (0)15 (100)10.56 e7.89, 14.13 e2.3417.880 (0)
Cd0.0820.12, 0.35 19 (100)0 (0)NANANANA0 (0)
Cs0.00240.0034, 0.010 6 (32)13 (68)0.00770.0050, 0.0120.00480.0240 (0)
Ca0.00220.0033, 0.0096 0 (0)19 (100)0.18 e0.075, 0.42 e0.00601.330 (0)
Ce0.00240.0034, 0.010 18 (95)1 (5)0.0000420.0000000052, 0.350.0150.0150 (0)
Cl0.00190.0028, 0.0082 0 (0)19 (100)0.38 e0.14, 1.07 e0.02317.130 (0)
Cr0.00130.0019, 0.0055 10 (53)9 (47)0.00200.0013, 0.00320.00190.00860 (0)
Co0.000960.0014, 0.0041 15 (79)4 (21)0.000930.00047, 0.00190.00150.00320 (0)
Cu0.00160.0023, 0.0067 6 (32)13 (68)0.00430.0025, 0.00760.00250.0480 (0)
In0.120.18, 0.52 19 (100)0 (0)NANANANA0 (0)
Fe0.00160.0024, 0.0071 0 (0)19 (100)0.26 e0.12, 0.57 e0.0221.690 (0)
Pb0.00490.0071, 0.021 6 (32)13 (68)0.0140.0088, 0.0210.00990.110 (0)
Mg0.00500.0072, 0.021 5 (26)14 (74)0.0320.016, 0.0650.0110.200 (0)
Mn0.00180.0025, 0.0075 6 (32)13 (68)0.00830.0040, 0.0170.00340.0540 (0)
Mo0.0120.017, 0.051 19 (100)0 (0)NANANANA0 (0)
Ni0.00100.0015, 0.0043 10 (53)9 (47)0.00170.0013, 0.00230.00200.00380 (0)
P0.00240.0036, 0.011 5 (26)14 (74)0.0110.0061, 0.0210.00450.0640 (0)
K0.00190.0028, 0.0083 0 (0)19 (100)1.44 e0.94, 2.18 e0.385.860 (0)
Rb0.00230.0034, 0.010 9 (47)10 (53)0.00430.0022, 0.00810.00430.0280 (0)
Se0.00220.0033, 0.0097 12 (63)7 (37)0.00330.0026, 0.00410.00390.00700 (0)
Si0.00640.0093, 0.027 0 (0)19 (100)1.08 e0.58, 2.00 e0.145.150 (0)
Ag0.0550.079, 0.24 19 (100)0 (0)NANANANA0 (0)
Na0.0100.015, 0.045 2 (11)17 (89)0.130.088, 0.190.0340.370 (0)
Sr0.00300.0043, 0.013 17 (89)2 (11)0.00150.00025, 0.00880.00750.00920 (0)
S0.00260.0038, 0.011 0 (0)19 (100)2.77 e2.20, 3.48 e0.994.790 (0)
Sn0.180.26, 0.76 19 (100)0 (0)NANANANA0 (0)
Ti0.000850.0012, 0.0036 2 (11)17 (89)0.0210.0088, 0.0500.00180.190 (0)
V0.00110.0015, 0.0046 9 (47)10 (53)0.00210.0012, 0.00390.00200.0130 (0)
Zn0.00150.0022, 0.0066 0 (0)19 (100)0.059 e0.039, 0.089 e0.0190.390 (0)
Abbreviations: Al, aluminum; Sb, antimony; As, arsenic; Ba, barium; BC, black carbon; Br, bromine; BrC, brown carbon; Cd, cadmium; Cs, cesium; Ca, calcium; Ce, cerium; Cl, chlorine; Cr, chromium; Co, cobalt; CI, confidence interval; Cu, copper; GM, geometric mean; In, indium; Fe, iron; Pb, lead; LDL, lower detection limit; Mg, magnesium; Mn, manganese; Max, maximum; Min, minimum; Mo, molybdenum; Ni, nickel; NA, not applicable; PM2.5, particulate matter with an aerodynamic diameter less than 2.5 μm; P, phosphorus; K, potassium; Rb, rubidium; Se, selenium; Si, silicon; Ag, silver; Na, sodium; Sr, strontium; S, sulfur; Sn, tin; Ti, titanium; UDL, upper detection limit; V, vanadium; and Zn, zinc. a The filter of one inside sample tore and could not be analyzed, and so that home was excluded from analyses. Of the remaining 19 samples, 16 were from inside and three were from outside the homes. b Estimated via simple (i.e., unadjusted), intercept only Tobit regression models of the natural logarithm transformed values. c Calculated from samples that had values at or between the LDL and UDL. d The UDL mass was 80 μg and the UDL concentration range was 116.08 to 344.21 μg/m3. e Estimated via simple (i.e., unadjusted), intercept only linear regression models of the natural logarithm transformed values.
Table
Table 3. Associations between the mean of samples inside homes a and smokers in the home and the number of smokers in the home at a brick kiln in Bhaktapur, Nepal (May 2019).
Table 3. Associations between the mean of samples inside homes a and smokers in the home and the number of smokers in the home at a brick kiln in Bhaktapur, Nepal (May 2019).
Smokers in HomeNumber of Smokers in Home
NoYes
PM2.5 Chemical Component, μg/m3GM b95% CI bGM b95% CI bp-Value bGMR b,c95% CI b,cp-Value b
Al0.100.043, 0.230.880.38, 2.040.00032.501.33, 4.710.005
As1.00Reference2.66 d,e0.30, ∞ d,eNA4.21 d0.80, 235.33 dNA
Ba0.00640.0026, 0.0160.0370.018, 0.0760.0032.191.31, 3.670.003
BC4.811.65, 13.9880.2224.43, 263.430.00065.671.55, 20.750.009
Br0.015 f0.010, 0.021 f0.038 f0.027, 0.054 f0.001 f1.41 f1.05, 1.90 f0.03 f
BrC11.32 f8.99, 14.25 f14.92 f10.78, 20.66 f0.15 f1.25 f0.93, 1.66 f0.12 f
Cs0.00450.0025, 0.00800.0120.0068, 0.0190.021.591.12, 2.260.009
Ca0.060 f0.021, 0.17 f0.53 f0.19, 1.49 f0.006 f2.59 f1.22, 5.50 f0.02 f
Ce1.00Reference1.00 d,e0.053, ∞ d,eNA1.21 d0.034, 6.51 dNA
Cl0.083 f0.035, 0.20 f3.26 f1.38, 7.75 f<0.0001 f3.86 f1.58, 9.42 f0.006 f
Cr0.000970.00045, 0.00210.00320.0022, 0.00480.0051.531.06, 2.210.02
Co1.00Reference2.66 d,e0.30, ∞ d,eNA4.21 d0.80, 235.33 dNA
Cu0.00220.0013, 0.00380.0120.0076, 0.019<0.00011.661.01, 2.730.05
Fe0.086 f0.034, 0.21 f0.72 f0.29, 1.79 f0.003 f2.49 f1.26, 4.94 f0.01 f
Pb0.00690.0035, 0.0130.0260.015, 0.0450.0021.490.93, 2.380.10
Mg0.0140.0059, 0.0340.0670.029, 0.150.011.901.03, 3.500.04
Mn0.00310.0013, 0.00740.0210.0097, 0.0450.0012.351.34, 4.130.003
Ni0.00110.00069, 0.00180.00230.0017, 0.00310.011.281.01, 1.610.04
P0.00420.0022, 0.00810.0290.016, 0.052<0.00012.211.36, 3.580.001
K0.91 f0.52, 1.60 f2.62 f1.49, 4.61 f0.01 f1.62 f1.08, 2.42 f0.02 f
Rb0.00170.00060, 0.00510.00950.0045, 0.0200.0082.021.14, 3.570.02
Se0.00230.0014, 0.00400.00370.0027, 0.00510.111.070.83, 1.390.59
Si0.48 f0.23, 0.96 f2.32 f1.15, 4.71 f0.004 f1.98 f1.17, 3.35 f0.01 f
Na0.140.078, 0.270.0960.051, 0.180.361.010.66, 1.550.96
Sr1.00Reference1.00 d,e0.053, ∞ d,eNA2.28 d,e0.93, ∞ d,eNA
S2.21 f1.69, 2.88 f3.64 f2.79, 4.76 f0.01 f1.25 f1.04, 1.52 f0.02 f
Ti0.00630.0024, 0.0160.0660.026, 0.170.00052.761.38, 5.520.004
V0.000770.00029, 0.00200.00480.0028, 0.00830.0012.061.32, 3.200.002
Zn0.035 f0.021, 0.061 f0.10 f0.060, 0.18 f0.01 f1.46 f0.95, 2.23 f0.08 f
Abbreviations: Al, aluminum; As, arsenic; Ba, barium; BC, black carbon; Br, bromine; BrC, brown carbon; Cs, cesium; Ca, calcium; Ce, cerium; Cl, chlorine; Cr, chromium; Co, cobalt; CI, confidence interval; Cu, copper; GM, geometric mean; GMR, geometric mean ratio; Fe, iron; Pb, lead; Mg, magnesium; Mn, manganese; Ni, nickel; NA, not applicable; PM2.5, particulate matter with an aerodynamic diameter less than 2.5 μm; P, phosphorus; K, potassium; Rb, rubidium; Se, selenium; Si, silicon; Na, sodium; Sr, strontium; S, sulfur; Ti, titanium; V, vanadium; and Zn, zinc. a The filter of one sample tore and could not be analyzed, so that home was excluded from analyses. b Estimated via simple (i.e., unadjusted) Tobit regression models of the natural logarithm transformed values. c Exponentiated regression coefficient and 95% CI (i.e., GM PM2.5 chemical component concentration ratio for a specified change in the independent variable or exp(β) − 1 = percent change in GM PM2.5 chemical component concentration for a specified change in the independent variable). d Exact odds ratio and 95% CI; estimated via simple (i.e., unadjusted) exact unconditional logistic regression models. e Median unbiased estimate. f Estimated via simple (i.e., unadjusted) linear regression models of the natural logarithm transformed values.
Table
Table 4. Associations between the mean of samples inside or outside homes a and fuel type and location at a brick kiln in Bhaktapur, Nepal (May 2019).
Table 4. Associations between the mean of samples inside or outside homes a and fuel type and location at a brick kiln in Bhaktapur, Nepal (May 2019).
Fuel Type and Location
LPG, IndoorWood, IndoorOutdoor LPG, Indoor vs. Wood, IndoorLPG, Indoor vs. OutdoorWood, Indoor vs. Outdoor
PM2.5 Chemical Component, μg/m3GM b95% CI bGM b95% CI bGM b95% CI bp-Value bp-Value b,cp-Value b,cp-Value b,c
Al0.140.062, 0.331.480.44, 4.980.370.074, 1.850.0070.0050.560.37
As1.00Reference6.36 d,e0.70, ∞d,effNANANANA
Ba0.00880.0047, 0.0160.0620.028, 0.140.0310.011, 0.0890.00050.00040.110.56
BC6.272.73, 14.41349.0464.46, 1,889.915.361.02, 28.210.0001<0.00010.980.002
Br0.018 g0.013, 0.025 g0.043 g0.026, 0.072 g0.013 g0.0069, 0.025 g0.01 g0.02 g0.67 g0.02 g
BrC12.03 g9.09, 15.91 g17.52 g6.93, 44.32 g5.54 g3.24, 9.47 g0.03 g0.68 g0.04 g0.09 g
Cs0.00520.0033, 0.00810.0150.0085, 0.0280.0120.0055, 0.0280.0090.010.150.91
Ca0.081 g0.032, 0.21 g1.01 g0.25, 4.11 g0.17 g0.028, 1.06 g0.02 g0.02 g0.72 g0.26 g
Ce1.00Reference2.20 d,e0.12, ∞ d,effNANANANA
Cl0.17 g0.072, 0.42 g5.86 g1.59, 21.52 g0.071 g0.013, 0.38 g0.0003 g0.0006 g0.59 g0.001 g
Cr0.00130.00071, 0.00230.00390.0023, 0.00660.00340.0016, 0.00710.010.010.090.95
Co1.00Reference6.36 d,e0.70, ∞ d,e12.47 d,e1.31, ∞ d,eNANANANA
Cu0.00320.0019, 0.00540.0150.0075, 0.0300.00200.00064, 0.00640.00060.0010.740.009
Fe0.12 g0.051, 0.28 g1.25 g0.35. 4.44 g0.33 g0.064, 1.69 g0.02 g0.01 g0.48 g0.38 g
Pb0.00950.0061, 0.0150.0360.020, 0.0640.0140.0061, 0.0310.0020.0010.700.15
Mg0.0170.0083, 0.0360.110.040, 0.300.0540.014, 0.210.010.0090.300.68
Mn0.00420.0022, 0.00770.0400.017, 0.0900.0150.0048, 0.044<0.0001<0.00010.120.33
Ni0.00150.0011, 0.00210.00210.0014, 0.00330.00280.0016, 0.00470.11NANANA
P0.00610.0036, 0.0100.0450.022, 0.0920.0170.0065, 0.045<0.0001<0.00010.150.25
K0.98 g0.67, 1.45 g4.17 g2.34, 7.43 g0.98 g0.46, 2.06 g0.001 g0.001 g>0.99 g0.01 g
Rb0.00270.0016, 0.00460.0180.011, 0.0310.00480.0022, 0.010<0.0001<0.00010.460.01
Se0.00310.0023, 0.00420.00320.0022, 0.00480.00390.0025, 0.00620.71NANANA
Si0.60 g0.30, 1.20 g3.58 g1.28, 9.97 g1.23 g0.33, 4.62 g0.03 g0.02 g0.58 g0.39 g
Na0.130.079, 0.210.0970.046, 0.200.210.083, 0.540.44NANANA
Sr1.00Reference2.20 d,e0.12, ∞ d,e3.67 d,e0.19, ∞ d,eNANANANA
S2.35 g1.80, 3.06 g4.29 g2.90, 6.35 g2.45 g1.47, 4.06 g0.04 g0.04 g0.99 g0.18 g
Ti0.00880.0037, 0.0210.130.036, 0.460.0280.0052, 0.150.0030.0020.460.34
V0.00130.00079, 0.00220.00750.0043, 0.0130.00350.0017, 0.0075<0.0001<0.00010.080.25
Zn0.039 g0.026, 0.060 g0.15 g0.084, 0.28 g0.053 g0.024, 0.12 g0.004 g0.003 g0.75 g0.09 g
Abbreviations: Al, aluminum; As, arsenic; Ba, barium; BC, black carbon; Br, bromine; BrC, brown carbon; Cs, cesium; Ca, calcium; Ce, cerium; Cl, chlorine; Cr, chromium; Co, cobalt; CI, confidence interval; Cu, copper; GM, geometric mean; Fe, iron; Pb, lead; LPG, liquefied petroleum gas; Mg, magnesium; Mn, manganese; Ni, nickel; NA, not applicable; PM2.5, particulate matter with an aerodynamic diameter less than 2.5 μm; P, phosphorus; K, potassium; Rb, rubidium; Se, selenium; Si, silicon; Na, sodium; Sr, strontium; S, sulfur; Ti, titanium; V, vanadium; and Zn, zinc. a The filter of one inside sample tore and could not be analyzed, so that home was excluded from analyses. Of the remaining 19 samples, 16 were from inside and three were from outside the homes. b Estimated via simple (i.e., unadjusted) Tobit regression models of the natural logarithm transformed values. c Used the Tukey-Kramer (for Tobit regression models) or Tukey (for linear regression models) methods to adjust for multiple comparisons. d Exact odds ratio and 95% CI; estimated via simple (i.e., unadjusted) exact unconditional logistic regression models. e Median unbiased estimate. f Degenerate; unable to estimate. g Estimated via simple (i.e., unadjusted) linear regression models of the natural logarithm transformed values.
Table
Table 5. Associations between the mean of samples inside homes a and smokers in home and fuel type, mutually adjusted for each other at a brick kiln in Bhaktapur, Nepal (May 2019).
Table 5. Associations between the mean of samples inside homes a and smokers in home and fuel type, mutually adjusted for each other at a brick kiln in Bhaktapur, Nepal (May 2019).
Smokers in HomeFuel Type
PM2.5 Chemical Componentp-Value bp-Value b
Al0.080.09
Ba0.230.03
BC0.220.002
Br0.04 c0.30 c
BrC0.30 c0.55 c
Cs0.390.12
Ca0.20 c0.08 c
Cl0.002 c0.06 c
Cr0.100.20
Cu0.0030.22
Fe0.14 c0.09 c
Pb0.130.10
Mg0.390.09
Mn0.220.008
Ni0.020.62
P0.020.02
K0.50 c0.02 c
Rb0.680.002
Se0.050.24
Si0.16 c0.09 c
Na0.500.99
S0.32 c0.09 c
Ti0.120.04
V0.070.004
Zn0.37 c0.03 c
Abbreviations: Al, aluminum; Ba, barium; BC, black carbon; Br, bromine; BrC, brown carbon; Cs, cesium; Ca, calcium; Cl, chlorine; Cr, chromium; Cu, copper; Fe, iron; Pb, lead; Mg, magnesium; Mn, manganese; Ni, nickel; PM2.5, particulate matter with an aerodynamic diameter less than 2.5 μm; P, phosphorus; K, potassium; Rb, rubidium; Se, selenium; Si, silicon; Na, sodium; S, sulfur; Ti, titanium; V, vanadium; and Zn, zinc. a The filter of one sample tore and could not be analyzed, so that home was excluded from analyses. b Estimated via multivariable Tobit regression models of the natural logarithm transformed values adjusted for smokers in the home and fuel type. c Estimated via multivariable linear regression models of the natural logarithm transformed values adjusted for smokers in the home and fuel type.
Table
Table 6. Associations between the mean of samples inside homes a and the number of smokers in the home and fuel type, mutually adjusted for each other at a brick kiln in Bhaktapur, Nepal (May 2019).
Table 6. Associations between the mean of samples inside homes a and the number of smokers in the home and fuel type, mutually adjusted for each other at a brick kiln in Bhaktapur, Nepal (May 2019).
Number of Smokers in HomeFuel Type
PM2.5 Chemical Componentp-Value bp-Value b
Al0.350.04
Ba0.300.02
BC0.720.002
Br0.48 c0.11 c
BrC0.30 c0.99 c
Cs0.300.14
Ca0.46 c0.06 c
Cl0.32 c0.02 c
Cr0.500.07
Cu0.980.01
Fe0.39 c0.06 c
Pb0.650.004
Mg0.770.04
Mn0.390.005
Ni0.090.82
P0.270.006
K0.75 c0.01 c
Rb0.920.0007
Se0.570.82
Si0.43 c0.06 c
Na0.510.37
S0.51 c0.07 c
Ti0.390.02
V0.200.002
Zn0.70 c0.008 c
Abbreviations: Al, aluminum; Ba, barium; BC, black carbon; Br, bromine; BrC, brown carbon; Cs, cesium; Ca, calcium; Cl, chlorine; Cr, chromium; Cu, copper; Fe, iron; Pb, lead; Mg, magnesium; Mn, manganese; Ni, nickel; PM2.5, particulate matter with an aerodynamic diameter less than 2.5 μm; P, phosphorus; K, potassium; Rb, rubidium; Se, selenium; Si, silicon; Na, sodium; S, sulfur; Ti, titanium; V, vanadium; and Zn, zinc. a The filter of one sample tore and could not be analyzed, so that home was excluded from analyses. b Estimated via multivariable Tobit regression models of the natural logarithm transformed values adjusted for the number of smokers in the home and fuel type. c Estimated via multivariable linear regression models of the natural logarithm transformed values adjusted for the number of smokers in the home and fuel type.
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Johnston, J.D.; Beard, J.D.; Montague, E.J.; Sanjel, S.; Lu, J.H.; McBride, H.; Weber, F.X.; Chartier, R.T. Chemical Composition of PM2.5 in Wood Fire and LPG Cookstove Homes of Nepali Brick Workers. Atmosphere 2021, 12, 911. https://doi.org/10.3390/atmos12070911

AMA Style

Johnston JD, Beard JD, Montague EJ, Sanjel S, Lu JH, McBride H, Weber FX, Chartier RT. Chemical Composition of PM2.5 in Wood Fire and LPG Cookstove Homes of Nepali Brick Workers. Atmosphere. 2021; 12(7):911. https://doi.org/10.3390/atmos12070911

Chicago/Turabian Style

Johnston, James D., John D. Beard, Emma J. Montague, Seshananda Sanjel, James H. Lu, Haley McBride, Frank X. Weber, and Ryan T. Chartier. 2021. "Chemical Composition of PM2.5 in Wood Fire and LPG Cookstove Homes of Nepali Brick Workers" Atmosphere 12, no. 7: 911. https://doi.org/10.3390/atmos12070911

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