A novel in-situ method to determine the respiratory tract deposition of carbonaceous particles reveals dangers of public commuting in highly polluted megacity
Particle and Fibre Toxicology volume 19, Article number: 61 (2022)
Exposure to air pollutants is one of the major environmental health risks faced by populations globally. Information about inhaled particle deposition dose is crucial in establishing the dose–response function for assessing health-related effects due to exposure to air pollution.
This study aims to quantify the respiratory tract deposition (RTD) of equivalent black carbon (BC) particles in healthy young adults during a real-world commuting scenario, analyze factors affecting RTD of BC, and provide key parameters for the assessment of RTD.
A novel in situ method was applied to experimentally determine the RTD of BC particles among subjects in the highly polluted megacity of Metro Manila, Philippines. Exposure measurements were made for 40 volunteers during public transport and walking.
The observed BC exposure concentration was up to 17-times higher than in developed regions. The deposition dose rate (DDR) of BC was up to 3 times higher during commute inside a public transport compared to walking (11.6 versus 4.4 μg hr−1, respectively). This is twice higher than reported in similar studies. The average BC mass deposition fraction (DF) was found to be 43 ± 16%, which can in large be described by individual factors and does not depend on gender.
Commuting by open-sided public transport, commonly used in developing regions, poses a significant health risk due to acquiring extremely high doses of carcinogenic traffic-related pollutants. There is an urgent need to drastically update air pollution mitigation strategies for reduction of dangerously high emissions of BC in urban setting in developing regions. The presented mobile measurement set-up to determine respiratory tract deposition dose is a practical and cost-effective tool that can be used to investigate respiratory deposition in challenging environments.
Exposure to air pollution has been recognized as a significant contributor to the global burden of disease , causing three  to nine  million deaths worldwide. To investigate the association of exposure to air pollution with adverse health effects, researchers have long relied on particulate matter (PM) with an aerodynamic diameter of less than 2.5 μm (PM2.5) . However, more and more pieces of evidence arise indicating that individual components of PM2.5 may have unequal health effects [5, 6]. Additional segregation between PM constituents may help better understand the health impacts of air pollution . The International Agency for Research on Cancer (IARC) has listed fine dust, i.e., traffic-related particulates, as carcinogenic to humans (IARC Group 1) because of its high content of heavy metals and sulfur oxides , causing a particularly negative effect on human health . Several studies proposed that black carbon, a major component of traffic-related emissions, may act as a carrier of carcinogenic compounds [10, 11]. However, black carbon exposure has been studied less than PM, therefore, their real effects are not yet established and are not included in the estimation of mortality rates.
Exposure can be quantified as a time-weighted concentration experienced by a person in a microenvironment, which is a function of the frequency, intensity, and duration of contact with a pollutant . A large fraction (up to 30%) of air pollution exposure to black carbon is experienced during transportation or commuting . Transport microenvironments (TMEs) such as walking, cycling, car, bus, and open-sided vehicles, are the most common modes of local transportation. Most of the existing review articles that assess pollutant exposures in TMEs are conducted in developed regions (e.g., Europe ). In low-to-middle income regions (LMIR) pollution exposure assessments remain limited. Because of the different vehicle fleet compositions, road configurations, and driving behavior in LMIR, the TME exposure studies conducted elsewhere may not be applicable.
To better understand the effects of air pollution exposure on human health, it is crucial to determine how much of the inhaled pollutants that are deposited in the respiratory tract. A common practice for assessing the respiratory tract deposition (RTD) of pollutants is to either apply numerical (in silico) or semi-empirical models (e.g., International Commission of Radiological Protection  and Multiple-Path Particle Dosimetry models ) or to perform laboratory and real-life in situ experiments involving human subject (e.g., RESPI , MERDOC , single breath measurement ). Additionally, other prior approaches (ab initio)  were used in some studies, however, the assumptions made (i.e., all inhaled particles are deposited) make such methods more susceptible to large uncertainties. Choosing one of the methods to estimate RTD depends on application and requirements, and while each method poses its advantages and disadvantages, in situ measurements arguably have the least assumptions among other available methods. In experiments involving humans, the complexity of the respiratory system, which depends on various conditions, can be fully represented. With that being said, in situ-based RTD assessments are usually more complicated to execute due to the involvement of human subjects, the requisite for ethical approval, and often an expensive and complex experimental setup. This may be the reason for only limited RTD studies in LMIR. Without in situ measurements, important parameters, e.g., particle uptake kinetics and personal breathing pattern, which are dependent on physiology and ethnicity, remain unknown, which may increase the uncertainties in the assessment of deposition dose.
A review of in situ RTD studies over the past years (Additional file 1: Tables S1–S2) shows that most of the studies were performed in laboratory setups with predefined exposure concentrations [21, 22], aerosol sources [17, 19, 21,22,23,24], and were mostly limited to passive activity, e.g., sitting [22, 23, 25,26,27]. Most importantly, no previously conducted studies were designed to reflect a real-world exposure scenario, i.e., RTD in a microenvironment during actual daily activity. Due to the complexity of aerosol in situ RTD studies, the majority of published experiments were done on a limited number of study participants (n < 10). It becomes evident that the information about RTD studies in real-world scenarios remains scarce. This is especially critical for developing regions, where high exposure concentrations and air quality continually worsens . As highlighted in the recent update of air quality guidelines by the World Health Organization (WHO) , it is vital to assess the shape of exposure–response relationships at both low and high air pollution levels. Assessing the real exposure and real lung deposition of pollutants will help in establishing exposure profiles, especially to represent the complex LMIR environments. This study serves as a step towards understanding the health effects of exposure to extremely high concentrations of carbonaceous particles in outdoor air in developing regions.
To improve the understanding of RTD in highly polluted environments, we deployed our previously developed method (MERDOC ) focusing on the respiratory deposition of equivalent black carbon (BC) particles in different TMEs. Metro Manila, the capital of the Philippines, was chosen as the study domain, representing LMIR in Southeast Asia. Metro Manila is a highly polluted urban environment [29, 30], with main air constituents, e.g., ultrafine particles, BC, originating from the most commonly used public utility vehicle (PUV, Jeepney) , which is powered by old-technology diesel engines. High exposure concentrations, combined with elongated commuting times are expected to pose a significant health risk that many developing megacities have not yet assessed.
The aims of this study are to 1) quantify RTD of BC mass in healthy young adults during a real-world commuting scenario and 2) analyze factors (including both physical and environmental) affecting RTD of BC. The results from this study provide insights into the respiratory tract deposition of carbonaceous particles in different TMEs. Above all, this study raises the awareness of air pollution in developing regions, provides information on the physical respiratory parameters of young adults, and provides data to assess health-related effects due to exposure to high concentrations of BC.
In this randomized, crossover study, a total of 45 study participants aged between 18 to 27 years were recruited for investigation of RTD of BC particles during their public commute (only 40 were qualified and selected for the data analysis). Exposure scenarios (starting in a clean or polluted environment) were randomly assigned to each subject on predetermined commuting routes choosing from modes of transportation, i.e., riding public transport and walking. A self-administered questionnaire was used to collect basic information, including name, gender, age, and history of cardiovascular or other diseases. All study participants were subjectively healthy and had no reported history of disease that might affect the lung function or the experiment. The subjects were selected according to the following criteria: no reported history of smoking; no physician-diagnosed cardiovascular, pulmonary, neurological, or other chronic diseases; and non-obese. Prior to the study, informed consent was obtained from all subjects.
The breathing parameters (calculated from exhaled airflow rate), personal exposure, and respiratory tract deposition of BC were measured using a previously developed measurement system to quantify real-world respiratory tract deposition dose of black carbon (MERDOC). A comprehensive description of the measurement system and data evaluation can be found in Madueño et al. . Several minor changes were made to the previous version of MERDOC (e.g., installation of a bypass for exhaled air, water trap, and double aerosol dryer), which both allowed better aerosol drying and improved system operability without compromising data quality. Briefly, the ambient aerosol is inhaled exclusively through the nose during normal tidal breathing, which is then exhaled through the mouthpiece (i.e., unidirectional flow) into a mixing chamber (filled with silica gel for drying, Fig. 1).
Carbonaceous aerosol particles were sampled from the stream of air at ambient pressure using a micro-aethalometer (model MA200, AethLabs, San Francisco, CA, USA; at a flow rate of 100 ml/min). Exposure concentrations of BC were monitored separately in parallel to exhaled air measurements. Data acquisition (logging BC mass concentrations, relative humidity, and temperature of sampled aerosol, as well as position in 1 s time resolution) was accomplished by 3 separate micro-computers, equipped with MERDOC systems. Two units of mobile MERDOC measurement systems were carried along the predetermined commuting routes by two volunteers (bringing instruments to measure exhaled BC mass concentration) and an experiment supervisor (bringing instruments to measure ambient BC mass concentration). The study participants were instructed on how to properly handle and use the MERDOC measurement system prior to the experiment. Mode of transportation (start and end times; based on position and speed information), exposure and exhaled BC mass concentrations, as well as breathing parameters were determined from recorded MEDOC data in the data evaluation step.
Aerosol particle losses in the instrument for both exhaled air and ambient aerosols, at different airflow rates across the mixing chamber (mimicking real-world exhaled airflow rate), were evaluated in the laboratory prior to the measurement campaign (Additional file 1: Fig. S1). The results from intercomparison between ambient and exhaled BC mass concentration measurement systems are available in Additional file 1: Figs. S2–S3. Additionally, the flow rate of exhaled air through HEPA filter 3 (Fig. 1, bypass line) was evaluated prior to (dry-state), during (moist-state), and after (moist-state) the experiment using Gillian Gilibrator-2 (Sensidyne, St. Petersburg, FL, US) primary standard airflow calibrator (Additional file 1: Fig. S4). No change in flow rate was observed with respect to HEPA filter wetting. The true exhaled airflow rate was calculated from the ratio between supplied and measured flow rates at the system inlet and exhaled air sample line. Laboratory and field evaluations of measurement set-up confirmed inter-system agreement within 10%.
The measurement campaign was performed as part of the project “Transdisciplinary Approach to Mitigate Emissions of Black Carbon (TAME-BC) ” in Metro Manila, Philippines. The TAME-BC campaign was conducted during the dry season (November 2019–March 2020) in the Philippines. The stationary measurement sites were positioned in the passenger harbor of Manila North Port, Manila City, and on the street side of East Avenue, Quezon City (Fig. 2) to investigate the physical–chemical aerosol properties of a highly urbanized megacity. The exposure measurements presented in this study (from 6 January to 10 March 2020) were carried out within a 5 km radius from the stationary measurement sites. The measurements were conducted on non-rainy days to avoid the washout effects of rainfall on ambient particulate concentration  and the convenience of the study participants. During the whole measurement campaign, the daily median temperature and RH were 26 °C (23–31 °C) and 67% (48–82%), respectively.
The study participants were asked to commute in TMEs by (1) public transport; and (2) walking on a curbside (Fig. 1a, b). The commute in public transport was restricted to riding a Jeepney, an open-sided vehicle that serves as the cheapest and the most common means of public transportation in the Philippines. The commute by walking on the curbside was instructed to be as casual-paced as possible (average speed of 3.5 km h−1). The streets chosen for commuting were significant thoroughfares in Metro Manila with canyon-like topography representing a polluted road environment. In contrast, a clean environment was characterized by transiting in an open space surrounded by greenery (usually inside a gated university campus).
The study participants traveled on the predefined routes, either in Manila or Quezon City (Fig. 2), between 6 am and 6 pm, with the majority of the time between midday and 4 pm. The participants randomly chose to start commuting either in a polluted or clean environment, with their choice of transportation (e.g., riding public transport and then walking, or vice versa), with the prerequisite to cover both walking and a public transport ride in one trip. A total of 63 periods of walking (723 min) and 97 journeys by public transport (420 min) were made. The commuting routes took at least 30 min to complete. The study supervisor (measuring BC exposure concentration) and participants (measuring exhaled BC mass concentration) traveled closely together (i.e., sat together on public transport and walked closely together) to ensure that the measured ambient concentrations by the supervisor were a suitable estimate of the BC concentrations inhaled by the participants. Before each measurement session, the volunteers were given approx. 5 min to adjust to the equipment and feel comfortable. When volunteers were inevitably interrupted from breathing into the MERDOC system for various reasons, e.g., sneezing, feeling of dried throat, getting on or alighting public transport, the inlet of the MERDOC system was closed manually (by applying clamp-on silicon tubing). In the data analysis, such occasions were detected by negative and noisy flowrate (due to flow direction change in the system). Such events were excluded from data analysis.
In this study, the breathing parameters (breathing rate and exhaled air flowrate), personal exposure, and RTD of BC were measured in 45 volunteers; however, only 40 (20 males and 20 females) study participants passed the initial data quality screening (some volunteers interrupted measurements too frequently, resulting in poor representation of investigated parameters). The demographics of the qualified study participants are summarized in Table 1.
Measurement quality control
To achieve high-quality measurement data, the procedures described in Madueño et al.  i.e., flow calibration, leak check, reference system check, particle loss estimation, instrument intercomparison (both in the laboratory and ambient setting, Additional file 1: Figs. S1–S3) were followed. The measured exposure and exhaled BC mass concentrations, as well as the flowrate of exhaled air were synchronized by lag cross-correlation. A thorough manual screening of each breath was done, flagging noisy data for exclusion in the subsequent data analysis. The accuracy of this method was previously validated by Madueño et al. .
The experimentally determined exhaled air flow rate, personal exposure, and exhaled air mass concentration of BC were used to calculate in situ deposition dose rate (DDR) following Eq. 1:
where BCin and BCex are the BC mass concentrations (in μg m−3) of inhaled and exhaled air, respectively. Please note that here BCin is assumed to be equal to the measured ambient BC mass concentration. The volume of inhaled air (in m3) was calculated from the flowrate measurements (Q, in L min−1) of exhaled air starting at (t0) and ending at (t1). In this study, the minute ventilation (MV) was calculated assuming inhaled air volume is equal to exhaled air volume. The total deposition fraction (DF) was defined as the percentage of the amount of BC mass concentration that was not expired after exhalation, generally stated as:
The exposure to BC mass concentration, DDR, and DF was calculated in 1-min median values. Additionally, mean and standard deviation were calculated to compare this study’s results to previous work.
Data evaluation was performed using the R programming language and free software environment for statistical computing and graphics (R Core Team, 2015). The correlation analysis was calculated with Pearson’s product moment. The differences between groups were evaluated based on Wilcoxon rank sum test (also known as Mann–Whitney-U test) for independent variable comparisons, and Wilcoxon signed rank test for paired variable comparisons. The significances considered were those at the 0.01 level.
Results and discussion
General overview of BC exposure concentration in metro manila
During the TAME-BC campaign, the BC exposure concentration was assessed both at stationary sites and TMEs (i.e., public transportation and walking) in Manila and Quezon City. The temporal variation of BC measured at the stationary measurement sites (using multiple angle absorption photometer, MAAP; type 5012, Thermo Scientific Inc.) showed a pronounced diurnal pattern (Fig. 3), with the highest BC mass concentration during the morning rush hour and the lowest—during midday. The highest BC mass concentration (± standard deviation) was 19 ± 9.6 μg m−3 and 63.1 ± 17.4 μg m−3 in Manila North Port and East Avenue, respectively. There was no noticeable change in BC mass concentration between weekdays and weekends. A noticeably lower BC mass concentration was recorded in Manila North Port as a result of enhanced dilution from the nearby open water, versus the busy streetside with close proximity to the emission sources in Quezon City. Compared to other regions in the world, the BC seasonal average in Metro Manila is 25.7 ± 19.7 μg m−3 (dry season). This is 2 – 17 times higher than in urban and traffic sites in India (< 12 μg m−3) , China (< 5 μg m−3) , Europe (< 5 μg m−3) , and the USA (< 1.5 μg m−3) . It must be noted that the BC mass concentration presented in this study corresponds to 5 months of BC mass concentration measurements in the Philippines. The annual average remains unknown.
Mobile measurements of BC exposure concentration in TMEs showed an average value of 50.0 ± 62.6 μg m−3 (average for Manila City: 57.5 ± 68.7 μg m−3; and average for Quezon City: 36.7 ± 47.1 μg m−3). The observed exposure concentration in TMEs is up to twofold higher compared to values reported from stationary measurement sites. It may suggest that substituting mobile measurements with stationary sites in exposure assessment may not represent true exposure concentrations, especially during transportation. The spatial distribution of BC mass concentration in TMEs between cities is shown in Fig. 4.
Although the exposure experiment was focused on riding public transport and walking, there is an apparent difference in the BC exposure in TMEs between the cities. The discrepancy may be explained by the effect of street topography and micro-meteorology. The commuting route in Manila city was located on a major thoroughfare. Both sides of the street are occupied by tall buildings resulting in a deep street canyon geometry  (street aspect ratio (height/width) of approx. 2). Such a setting influences poor airflow across the street, thus, increasing the accumulation of pollutants. While in Quezon City, the commuting mostly took place on an open-spaced road  (street aspect ratio of less than 0.5).
Effect of activity on respiratory tract deposition
The descriptive statistics of MV, breathing rate (BR), tidal volume (TV), BC exposure concentration, DDR, and DF in different modes of transportation are summarized in Table 2 and Additional file 1: Fig. S5. The median BR values while riding public transport and slow walking, were 11.8 and 13 breaths min−1, respectively. The observed TV both resulted in 0.6 L breath−1, while the MV was 7.5 L min−1 and 8.1 L min−1 during public transport and walking, respectively. The effect of commuting mode on all breathing parameters was small and showed no statistically significant difference (p value > 0.01). A possible reason for the similarity in the breathing patterns between sitting inside public transport and light exercise (walking) is due to the configuration of passenger seats inside the Jeepney. The seats are not as comfortable as in a regular vehicle, and the orientation of passengers is seated sideways (Fig. 1a). This means that for every acceleration or deceleration of the PUV, the passengers must compensate for their sitting position, which may have caused slight physical activity similar to slow walking.
The BC mass concentration was more than twofold higher while commuting in PUV compared to walking (72 vs. 30 μg m−3, respectively). The DF of BC between different commuting modes was noticeably different (39% for a ride in public transport versus 44% for a commute by walking). The respiratory tract DDR of BC while riding PUV and walking was 12 μg hr−1 and 4 μg hr−1, respectively. The choice of commuting mode showed a statistically significant difference (p value < 0.01) between the BC exposure concentration, DF, and respiratory tract DDR. Suggesting that the respiratory tract DDR is primarily determined by respectively higher exposure concentrations of BC inside PUV compared to walking.
The measured breathing parameters, i.e., BR, TV, MV, in this study are comparable with previous studies (± 10%) where respiratory tract deposition of aerosol BC particles during spontaneous breathing on healthy subjects was measured (Table 3). However, if comparing the measured MV values to those reported in EPA Exposure Handbook , we can see that it is significantly different. Therefore, using standard reported values might result in errors when estimating respiratory tract deposition of Filipinos (underestimation when using MV for sitting; overestimation when using MV for exercise). Contrary to EPA Exposure Handbook, standard values reported by the International Commission on Radiological Protection (ICRP)  shows better agreement between reported and measured MV values (except for MV during exercise). The differences between measured and reported MV values may occur due to several reasons, e.g., considered range of metabolic activities, anthropometric and anatomical disparities of respiration related to ethnicity [41, 42]. Study design and measurement set-up to determine respiratory parameters could also influence the results (for further discussion, please refer to section Study Considerations). We thus recommend using MV values from this study or those reported by ICRP (while at rest) when calculating respiratory tract deposition of airborne pollutants in the Filipino population. For the studies, where breathing rate data relevant to the population considered is not available, authors shall conduct a sensitivity study evaluating the effects of the chosen breathing parameters onto respiratory tract deposition.
The measured DDR of BC in the respiratory tract of multiple subjects showed high variability, which is a result of changing exposure concentrations and subject-specific breathing parameters (Additional file 1: Fig. S7). The comparison of experimentally-measured RTD of hydrophobic particles segregated by activity (e.g., sitting, exercise) is presented in Additional file 1: Table S2, and the comparison between different assessment methods is summarized in Additional file 1: Table S3. Overall, the TV, BR, and exposure concentration of BC are some of the most important variables to estimate RTD. The breathing parameters are especially crucial when simulating RTD using dosimetry model, i.e., freely available Multiple-Path Particle Dosimetry model (MPPD ; (http://www.ara.com/products/mppd.htm)).
Effect of gender on respiratory tract deposition
The gender separated breathing parameters, BC exposure concentration, respiratory tract DDR, and DF are summarized in Table 4 and Additional file 1: Fig. S6. The MV, BR, and TV showed no statistically significant difference (p value > 0.01) and were 7.2 versus 6.9 L min−1, 11.8 versus 12.5 breath min−1, and 0.7 versus 0.6 L breath−1 for males and females, with a small to medium effect size (rrb = 0.1, 0.2, and 0.3), respectively.
The BC exposure of females was at 69.8 μg m−3, while males were at 57 μg m−3. Although the comparison between the exposure scenario showed no statistically significant difference between genders (p value > 0.01), the effect size is small (rrb ≤ 0.2). This means that in spite of the randomization of the exposure scenario, the erratic and high irregularities in traffic may have affected sporadic BC exposure of study participants. Interestingly, the corresponding respiratory tract DDR and DF of BC showed no statistically significant difference for males and females (p value > 0.01, 8.2 versus 8.3 μg hr−1, and 42% versus 40%, respectively). Nevertheless, the results show that despite the differences in the physiology of males and females (e.g., males have slightly higher TV but lower BR contrariwise to females), the practical effect is small (rrb ≤ 0.2). Each factor may balance each out, resulting in similar DDR and DF between genders. Similar results were also reported by Löndahl et al. . Moreover, the experimental and computational studies of Kim and Jacques , and Sturm  also reported essentially comparable total DF values between males and females for inhaled particles with a diameter greater than 80 nm.
There are several limitations to the MERDOC measurement system based on its design aspects . Firstly, the measurement can only determine the total mass deposition of BC particles in the entire respiratory tract, thus the information on regional lung deposition is unknown. Because of this, much desired dosimetry model evaluation based on experimental respiratory tract deposition measurements is not possible at this moment. To enable such model validation, ambient and exhaled BC PNSD must be known. This requires mobile aerosol instrumentation, capable to determine either PNSD and the mixing state of aerosol particles (BC PNSD can then be calculated) or BC PNSD itself. Although such instrumentation exists for stationary measurements, its portability to this moment is seriously limited. In general, one may try to estimate BC PNSD based on BC mass concentration measurements, assuming geometric mean diameter and standard deviation of BC particles, constraining reconstructed BC PNSD by the total measured mass of BC particles, however this requires a number of critical assumptions and is beyond the scope of this study. Moreover, in such way determined regional DF would be more of qualitative nature rather than means to validate dosimetry model. Stationary measurements could provide some advantage when estimating BC PNSD, however, neither in this study nor in previous works BC PNSD were determined in variety of environments covering multiple commuting scenarios. Secondly, for the exhaled BC concentration measurements, subjects had to inhale exclusively through nose, followed by exhalation through mouth into mouthpiece. Such measurement set-up might result in deviation from normal physiological breathing pattern, which in turn might influence determined minute ventilation, as well as respiratory tract deposition. With respect to respiratory deposition, the dominating mechanism for lung deposition of nanoparticles with diameter less than 500 nm is diffusion, which primarily takes place in the acinus (alveolar region; due to extended residence time). As hydrophobic BC particles have a mean geometric diameter of approx. 80–200 nm , their growth shall be limited during the inhalation and exhalation cycle in the respiratory tract. This means that deposition in the upper airways or the increased filtration efficiency through nasal breathing shall not significantly affect the BC deposition dose levels among mouth or nose breathers . It can also be demonstrated that mouth breathing and combined breathing show similar flow profiles, hence, the inhalation route does not affect the distribution of particles in the lower airways . It must be noted, however, that given the measurement set-up, which was optimized for mobile measurements and not standard laboratory lung function test, the measured tidal volume could deviate from real values. In the future, a comparison between MERDOC and more standardized systems (e.g., RESPI ) could help to further validate mobile respiratory tract deposition measurement set-up for field experiments.
Another limitation in this study is with regard to the experimental procedure. Although this study showcased one of the largest real-world in situ measurements of respiratory tract deposition in terms of the number of study participants, it was only limited to young healthy adults. Investigations of respiratory tract deposition in children, the elderly, and people with lung disorders could provide comprehensive information. The sampled breath of study participants, though instructed to be as natural as possible, was to a certain degree disturbed due to the use of a mouthpiece. Some experiments are using a similar technique, however, a thorough consideration of the experimental method must be noted when comparing breathing patterns and respiratory deposition dose with other studies.
Summary and conclusion
Establishing an exposure-dose relationship is critical to better understand the health response of inhaling particulate matter. Among several different methods to determine respiratory tract deposition dose, in situ measurements, albeit complicated, are arguably the best one, as it accounts for the complexity of the human respiratory system, ambient conditions, and particle physico-chemical properties. In this study, the respiratory tract deposition of BC particles under real-world conditions in the developing megacity of Metro Manila was investigated. The experiment was successfully conducted with 40 young, healthy adults during their commute by riding public transport and walking.
The observed roadside BC exposure concentration in this study is up to 17 times higher than in other studies [36, 37], and the deposition dose of BC is up to twice higher than in a comparable study . The study results showed that the mode of transportation, i.e., sitting inside public transport versus slow walking, had no significant influence on the BR, TV, and MV. The breathing parameters between genders also showed no statistically significant difference. Conversely, the respiratory tract deposition dose rate of BC is significantly higher in public transport than walking (Wilcoxon signed rank test p-value < 0.01). This is due to correspondingly higher BC exposure concentration inside public transport (72 μg m−3 versus 30 μg m−3, respectively). Thus, it would be advisable to choose walking as a mode of transportation for shorter trips, especially if this includes routes further away from the roadside. Regular users of public transport (Jeepney) should consider wearing high-quality facemasks equipped with high-efficiency particulate filters to reduce exposure. The comparison between measured true DDR of BC in different modes of transportation and alternative methods to estimate RTD highlights the importance of subject-specific breathing parameters and PNSD in the dosimetry calculations. Furthermore, miniaturization of current stationary aerosol instrumentation for PNSD and BC PNCD measurements would enable mobile in situ determination of both ambient and exhaled PNSD, which could be used for comprehensive dosimetry model evaluation.Additional file 1.
This study is the first attempt toward assessing the carbonaceous pollution-related health effects through the systematic in situ determination of real-world respiratory tract deposition dose of BC in developing regions. The provided information on respiratory tract deposition and breathing parameters can be used to advance epidemiological assessment of health risks of carbonaceous pollution.
Availability of data and materials
Processed and raw data are available upon request from the corresponding author.
Equivalent black carbon
Deposition dose rate
Respiratory tract deposition
Low-to-middle income regions
Transdisciplinary approach to mitigate emissions of black carbon
Abbafati C, Abbas KM, Abbasi-Kangevari M, Abd-Allah F, Abdelalim A, Abdollahi M, et al. Global burden of 87 risk factors in 204 countries and territories, 1990–2019: a systematic analysis for the Global Burden of Disease Study 2019. Lancet. 2020;396:1223–49.
Stanaway JD, Afshin A, Gakidou E, Lim SS, Abate D, Abate KH, et al. Global, regional, and national comparative risk assessment of 84 behavioural, environmental and occupational, and metabolic risks or clusters of risks for 195 countries and territories, 1990–2017: A systematic analysis for the Global Burden of Disease Stu. Lancet. 2018;392:1923–94.
Burnett R, Chen H, Szyszkowicz M, Fann N, Hubbell B, Pope CA, et al. Global estimates of mortality associated with longterm exposure to outdoor fine particulate matter. Proc Natl Acad Sci USA. 2018;115:9592–7.
AH Janssen N, E Gerlofs-Nijland M, Lanki T, O Salonen R, Cassee F, Hoek G, et al. HEALTH EFFECTS OF BLACK CARBON Health effects of black carbon. Who [Internet]. 2012; Available from: https://www.euro.who.int/__data/assets/pdf_file/0004/162535/e96541.pdf
Park M, Joo HS, Lee K, Jang M, Kim SD, Kim I, et al. Differential toxicities of fine particulate matters from various sources. Sci Rep. 2018;8:1–11.
Lelieveld J, Evans JS, Fnais M, Giannadaki D, Pozzer A. The contribution of outdoor air pollution sources to premature mortality on a global scale. Nature. 2015;525:367–71.
Anderson HR. Implications for the science of air pollution and health. Lancet Respir Med. 2017;5:916–8. https://doi.org/10.1016/S2213-2600(17)30396-X.
Loomis D, Grosse Y, Lauby-Secretan B, El GF, Bouvard V, Benbrahim-Tallaa L, et al. The carcinogenicity of outdoor air pollution. Lancet Oncol. 2013;14:1262–3. https://doi.org/10.1016/S1470-2045(13)70487-X.
Krzyzanowski M, Kuna-Dibbert B SJ. No Title. eds Heal Eff Transp air pollution. Copenhagen: WHO Regional Office for Europe; 2005.
WHO. Health relevance of particulate matter from various sources. Beilstein J Nanotechnol. 2007;5:1590–602.
Janssen NAH, Hoek G, Simic-Lawson M, Fischer P, van Bree L, Ten BH, et al. Black carbon as an additional indicator of the adverse health effects of airborne particles compared with pm10 and pm2.5. Environ Health Perspect. 2011;119:1691–9.
US EPA. Guidelines for Exposure Assessment, EPA/600/Z-92/001. Risk Assess Forum, Washington, DC, 1992 [Internet]. 1992;57:22888–938. Available from: http://ngha.med.sa/English/MedicalCities/AlMadinah/MedicalDepartments/Pages/default.aspx
Dons E, Int Panis L, Van Poppel M, Theunis J, Willems H, Torfs R, et al. Impact of time-activity patterns on personal exposure to black carbon. Atmos Environ. 2011;45:3594–602. https://doi.org/10.1016/j.atmosenv.2011.03.064.
de Nazelle A, Bode O, Orjuela JP. Comparison of air pollution exposures in active vs. passive travel modes in European cities: a quantitative review. Environ Int. 2017;99:151–60. https://doi.org/10.1016/j.envint.2016.12.023.
Bailey MR, Ansoborlo E, Guilmette RA, Paquet F. Updating the ICRP human respiratory tract model. Radiat Prot Dosimetry. 2007;127:31–4.
Anjilvel S, Asgharian B. A multiple-path model of particle deposition in the rat lung. Toxicol Sci. 1995;28:41–50.
Löndahl J, Pagels J, Swietlicki E, Zhou J, Ketzel M, Massling A, et al. A set-up for field studies of respiratory tract deposition of fine and ultrafine particles in humans. J Aerosol Sci. 2006;37:1152–63.
Madueño L, Kecorius S, Löndahl J, Müller T, Pfeifer S, Haudek A, et al. A new method to measure real-world respiratory tract deposition of inhaled ambient black carbon. Environ Pollut. 2019;248:295–303.
Jakobsson JKF, Hedlund J, Kumlin J, Wollmer P, Löndahl J. A new method for measuring lung deposition efficiency of airborne nanoparticles in a single breath. Sci Rep. 2016;6:1–10.
Kumar P. Dynamics of coarse and fi ne particle exposure in transport microenvironments. NPJ Clim Atmos Sci. 2018. https://doi.org/10.1038/s41612-018-0023-y.
Daigle CC, Chalupa DC, Gibb FR, Morrow PE, Oberdörster G, Utell MJ, et al. Ultrafine particle deposition in humans during rest and exercise. Inhal Toxicol. 2003;15:539–52.
Löndahl J, Pagels J, Boman C, Swietlicki E, Massling A, Rissler J, et al. Deposition of biomass combustion aerosol particles in the human respiratory tract. Inhal Toxicol. 2008;20:923–33.
Löndahl J, Massling A, Pagels J, Swietlicki E, Vaclavik E, Loft S. Size-resolved respiratory-tract deposition of fine and ultrafine hydrophobic and hygroscopic aerosol particles during rest and exercise. Inhal Toxicol. 2007;19:109–16.
Rissler J, Nicklasson H, Gudmundsson A, Wollmer P, Swietlicki E, Löndahl J. A set-up for respiratory tract deposition efficiency measurements (15–5000 nm) and first results for a group of children and adults. Aerosol Air Qual Res. 2017;17:1244–55.
Guo L, Johnson GR, Hofmann W, Wang H, Morawska L. Deposition of ambient ultrafine particles in the respiratory tract of children: A novel experimental method and its application. J Aerosol Sci. 2020;139:105465. https://doi.org/10.1016/j.jaerosci.2019.105465.
Rissler J, Gudmundsson A, Nicklasson H, Swietlicki E, Wollmer P, Löndahl J. Deposition efficiency of inhaled particles (15–5000 nm) related to breathing pattern and lung function: An experimental study in healthy children and adults. Part Fibre Toxicol. 2017;14:1–12.
Löndahl J, Massling A, Swietlicki E, Bräuner EV, Ketzel M, Pagels J, et al. Experimentally determined human respiratory tract deposition of airborne particles at a busy street. Environ Sci Technol. 2009;43:4659–64.
World Health Organization. WHO Global Air Quality Guidelines. Particulate matter (PM2.5 and PM10), ozone, nitrogen dioxide, sulfur dioxide and carbon monoxide. 2021.
Madueño L, Kecorius S, Birmili W, Müller T, Simpas J, Vallar E, et al. Aerosol particle and black carbon emission factors of vehicular fleet in Manila, Philippines. Atmosphere (Basel). 2019;10:1–15.
Kecorius S, Madueño L, Vallar E, Alas H, Betito G, Birmili W, et al. Aerosol particle mixing state, refractory particle number size distributions and emission factors in a polluted urban environment: Case study of Metro Manila, Philippines. Atmos Environ. 2017;170:169–83.
Kecorius S, Tamayo EG, Galvez MC, Madueño L, Betito G, Gonzaga-Cayetano M, et al. Activity pattern of school/university tenants and their family members in metro Manila, Philippines. Aerosol Air Qual Res. 2018;18:2412–9.
Tõnisson L, Kunz Y, Kecorius S, Madueño L, Tamayo EG, Casanova DM, et al. From transfer to knowledge co-production: A transdisciplinary research approach to reduce black carbon emissions in metro manila, philippines. Sustain. 2020;12:1–19.
Seinfeld JH, Pandis SN. Atmospheric chemistry and physics-from air pollution to climate change. New Jersey: Wiley; 2006.
Srivastava S, Kumar M, Singh RS, Rai BN, Mall RK, Banerjee T. Long-term observation of black carbon aerosols at an urban location over the central Indo-Gangetic Plain. South Asia Atmosfera. 2019;32:95–113.
Zhao S, Tie X, Cao J, Li N, Li G, Zhang Q, et al. Seasonal variation and four-year trend of black carbon in the Mid-west China: the analysis of the ambient measurement and WRF-Chem modeling. Atmos Environ. 2015;123:430–9. https://doi.org/10.1016/j.atmosenv.2015.05.008.
Kutzner RD, von Schneidemesser E, Kuik F, Quedenau J, Weatherhead EC, Schmale J. Long-term monitoring of black carbon across Germany. Atmos Environ. 2018;185:41–52. https://doi.org/10.1016/j.atmosenv.2018.04.039.
Levy ME, Zhang R, Khalizov AF, Zheng J, Collins DR, Glen CR, et al. Measurements of submicron aerosols in Houston, Texas during the 2009 SHARP field campaign. J Geophys Res Atmos. 2013;118:10518–34.
Vardoulakis S, Fisher BEA, Pericleous K, Gonzalez-Flesca N. Modelling air quality in street canyons: a review. Atmos Environ. 2003;37:155–82.
U.S. Environmental Protection Agency. September 2011 EXPOSURE FACTORS HANDBOOK : 2011 EDITION National Center for Environmental Assessment Office of Research and Development U.S. Environmental Protection Agency Washington, DC 20460 Exposure Factors Handbook. Exposure. 2011
Valentin J. Basic anatomical and physiological data for use in radiological protection: reference values. Ann ICRP. 2002;89(32):3–4.
Bennett WD, Zeman KL. Effect of race on fine particle deposition for oral and nasal breathing. Inhal Toxicol. 2005;17:641–8.
Korotzer B, Ong S, Hansen JE. Ethnic differences in pulmonary function in healthy nonsmoking Asian- Americans and European-Americans. Am J Respir Crit Care Med. 2000;161:1101–8.
Tobin MJ, Chadha TS, Jenouri G, Birch SJ, Gazeroglu HB, Sackner MA. Breathing patterns* 1. Normal subjects. Chest. 1983;84:202–5.
Rissler J, Swietlicki E, Bengtsson A, Boman C, Pagels J, Sandström T, et al. Experimental determination of deposition of diesel exhaust particles in the human respiratory tract. J Aerosol Sci. 2012;48:18–33.
Deng Q, Deng L, Miao Y, Guo X, Li Y. Particle deposition in the human lung: Health implications of particulate matter from different sources. Environ Res. 2019;169:237–45. https://doi.org/10.1016/j.envres.2018.11.014.
Kim CS, Jaques PA. Analysis of total respiratory deposition of inhaled ultrafine particles in adult subjects at various breathing patterns. Aerosol Sci Technol. 2004;38:525–40.
Sturm R. Total deposition of ultrafine particles in the lungs of healthy men and women: experimental and theoretical results. Ann Transl Med. 2016;4:1–10.
Everard ML, Hardy JG, Milner AD. Comparison of nebulized aerosol deposition in the lungs of healthy-adults following oral and nasal inhalation. Thorax. 1993;48(10):1045–6. https://doi.org/10.1136/thx.48.10.1045.
Lizal F, Elcner J, Jedelsky J, Maly M, Jicha M, Farkas Á, Belka M, Rehak Z, Adam J, Brinek A, Laznovsky J, Zikmund T, Kaiser J. The effect of oral and nasal breathing on the deposition of inhaled particles in upper and tracheobronchial airways. J Aerosol Sci. 2020;150: 105649.
We would like to acknowledge the help and support of Vincent M. Balanag Jr., MD in the procurement of Ethical Approval at the Lung Center of the Philippines. We would also like to extend our deepest appreciation to all the colleagues and study participants, who actively engaged in the experiment.
Open Access funding enabled and organized by Projekt DEAL. This research was funded by the German Federal Ministry of Education and Research in the framework of TAME-BC (project number 01LE1903A).
Ethics approval and consent to participate
Ethical approval for the study was issued by Lung Center of The Philippines, Institutional Ethics Review Board (LCP-IERB code: LCP-CS-024-2019). Consent to participate was obtained from all the study participants prior measurements. The study was carried out in accordance with a named standard: commonly the Declaration of Helsinki. Exception: Research gathered via questionnaires.
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. Experiment quality assurance and supplementary results. Table S1: List of related in situ respiratory tract deposition dose studies. Table S2: Summary of related in situ respiratory tract deposition studies using hydrophobic particles. Table S3: Mean DDR estimated using different assessment methods. Figure S1: Instrument laboratory intercomparison with reference system. Figure S2: Micro-aethalometer intercomparison in Leipzig, Germany. Figure S3: Micro-aethalometer intercomparison in Metro Manila, Philippines, using ambient street-site aerosol. Figure S4: Flow rate through dry and wet (after exposing to breath air) particulate filter. Figure S5: Descriptive statistics of measured parameters in TMEs between public transport and walking. Figure S6: Descriptive statistics of measured parameters separated between males and females. Figure S7: Deposition dose rate as a function of measured BC exposure concentrations.
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Madueño, L., Kecorius, S., Löndahl, J. et al. A novel in-situ method to determine the respiratory tract deposition of carbonaceous particles reveals dangers of public commuting in highly polluted megacity. Part Fibre Toxicol 19, 61 (2022). https://doi.org/10.1186/s12989-022-00501-x