We selected the location based on two different characteristic sites i.e. an educational and a residential area which have a possible influenced from various emission sources nearby as shown in Figure 1. The first sampling site was located in the 4^th floor of Environmental Engineering Division, Faculty of Engineering, Andalas University (00˚54'46.3''S 100˚27'50.0''E, 144.8 m a.s.l). Andalas University is the largest University in Sumatera Island which located in the top of the Limau Manis hill, around ± 3.41 km from the second sampling site and ±3.65 km from Cement Factory. In 2019, the total of active students at Andalas University was around 25,806 students and 3082 of them have registered in the Engineering faculty.

Furthermore, the second study area is situated in the northwest of Cement Factory (±1.3 km) and north of Padang Basi Street (±1.2 km) which located on the rooftop of one of the resident’s houses in Unand B Block residential area (0˚56'30.7''S 100˚27'17.0''E), 284.7 m above sea level (a.s.l), Limau Manis Selatan Village, in Pauh Subdistrict of Padang city. The site was ± 10.62 km from the city center. The total area of Limau Manis Selatan Village is around 12.96 Ha and around 11,663 total residence in 2018. As to the land use, the Pauh subdistrict area has used for field rice (991 Ha), garden (464 Ha), dry field rice (219 Ha), community forest (1927 Ha), unused (110 Ha), fish fond, state forest and others (10,366 ha) and non-agriculture i.e. road, residential area, institution, industrial area account 552 Ha (BPS Padang City, 2019). Cement factory nearby sampling site is the first cement factory in Indonesia (established in 1910) and the total production is more than million tons per year. Feedstock such as coal, gypsum, and limestone are the primary raw materials in the production of cement in Indonesia.

Published by Padang Statistical Agency (2019) (BPS Padang City, 2019), respiratory disease is the biggest number of patients in the Pauh Subdistrict which around 7.7 percent (5690 patients) of the total population (74,141).

Ambient Nano Sampler (ANS), a cascade air applicable to PM_0.1, developed by Furuuchi et al. (2010) was used for air sampling to collect the particle in Padang city, Indonesia. The sampler consists of four impactor stages to collect the particle > 10 μm, 10 - 2.5 μm, 2.5 - 1 μm, 1 - 0.5 μm, respectively from the top to the bottom of the sampler, and an inertial filter (IF) stage to specify the particle 0.5 - 0.1 μm before going down to the last stage called backup filter (BF) as the container of particle smaller than 0.1 μm (PM_0.1). A 55-mm quartz fibrous filter (QFF) (Pallflex, 2500 QAT-UP) was used for collection in each stage except for the IF stage which used a stainless-steel filter packed in an IF (SUS304, fiber diameter = 9.8 µm). Furthermore, the QFF filters were preheated at 350˚C to ignore the possible contaminant and kept it in the weighing chamber around 48 hours at a stable temperature and relative humidity at 21.5˚C ± 1.5˚C and 35% ± 5%, respectively before and after sampling (PWS-PM2.5, Tokyo Dylec Corp., Japan) following the procedure standard published by Ministry of Environment of Japan (2019) (MOE, 2019). 75 QFFs and 15 IFs were used in this study for around there weeks from 14^th to 25^th March in EA and from 8^th to 12^th March 2018 in RA. To control the possible contamination, travel blank filters were used and kept at the same box as the studied filters and kept at the temperature −20˚C until the chemical analyses performed. Both studied and blank filters were covered by aluminum foil and put in the zip-lock plastic bag during traveling time to/from the sampling site.

To obtain the carbon content in the size-fractionated particle in Padang city, a thermal/optical carbon analyzer (Model 5 L, Sunset Instruments Inc., USA) has been used following by Interagency Monitoring of Protected Visual Environments-Thermal/Optical Reflectance (IMPROVE-TOR) protocol. This method could specify four OC fractions as OC1 (120˚C), OC2 (250˚C), OC3 (450˚C), and OC4 (550˚C) and three different components of EC i.e. EC1 (550˚C), EC2 (700˚C), and EC3 (800˚C) (Han et al., 2007). The OC analyses were performed in pure helium (He) atmosphere while the EC was done in a mixture of O2 (2%) and He (98%) carrier gas (Watson et al., 2009). Furthermore, the pyrolysis organic carbon (PyOC) was determined after the reflected laser light gained its original intensity after O₂ added to the experimental atmosphere.

The total OC is OC1 + OC2 + OC3 + OC4 + PyOC while the total EC is EC1 + EC2 + EC3-PyOC. The char EC (EC1-PyOC) and soot-EC (EC2 + EC3) were also discussed in this study. The quality assurance and quality control (QA/QC) for carbon analysis were calibrated with a reference standard and blank filters. A reference chemical i.e. sucrose C₁₂H₂₂O₁₁) (196-00015, Sucrose, Wako Pure Chemical Industries, Ltd., Japan) was used for the calibration of carbon analyses while the blank filter was used to determine the minimum detection limit (MDLs) which is 0.9 and 0.02 μg/cm² for OC and EC, respectively. It means, those values were confirmed to be small enough to a filter blank value.

Open biomass burning as the sources of PMs also discuss by using the information detected by real-time hotspots from the Moderate Resolution Imaging Spectroradiometer (MODIS) satellite remote sensing imagery (available from http://earthdata.nasa.gov/data/near-real-time-data/firms) provided by US NASA (NASA, 2021). To examine the long air mass transport for the last 72-hour to the sampling site at 500 meters from the above ground level (to ensure the air mass from the sources arriving sampling sites was in the planetary boundary layer (PBL)), backward trajectory data evaluated by using the HYbrid Single-Particle Lagrangian Integrated Trajectory Model version-4 (HYSPLIT4) (ALR, 2020) were used in this study.

Mass concentrations of the size-segregated aerosol particle with their mean, standard deviations, minimum and maximum as well as their ratio in educational (EA) and residential (RA) areas are given in Table 1. The average mass concentration of each size fraction of particles is illustrated in Figure 2(a). PMs with different sizes were divided into six modes according to cut-off sizes of impactor stages, namely PM_>10, PM_10-2.5, PM_2.5-1, PM_1-0.5, PM_0.5-0.1, PM_0.1. The magnitudes of all particle size distribution of mass concentration in EA and RA have distinct peaks in the second stage (2.5 - 10 μm). As shown in Figure 2(b), the fine and coarse particle mode (>1 μm) was dominated the particle distribution in both sites. The PM level in RA was larger than that in EA. It might be attributed to the RA site location closer to pollutant sources as cement factory and Padang

Besi street while the EA site was located inside the Andalas University which located at the top of Limau Manis hills that is rather isolated from surrounding sources by green belt trees (see Figure 1).

The PMs concentrations in Padang city further compare to the WHO guidelines. Compare to the standard both in particular for PM_2.5 (25 μg/m³) and PM₁₀ (50 μg/m³) in ambient air for 24 hours, exceeded in all days for RA site which ranged from 35.82 - 48.49 μg/m³ and 58.72 - 85.35 μg/m³ for the PM_2.5 and PM₁₀, respectively (see Table 1) (WHO, 2006). In order, the average level of those two PMs in RA site was 42.30 ± 4.70 and 68.71 ± 10.99 μg/m³ which are comparable to the concentration in the residential area of Bangkok, Thailand at 40.9 ± 21.4; 41.5 ± 24.6 and 61 ± 25.2; 62.1 ± 30.7 μg/m³ respectively for PM_2.5 and PM₁₀ (Chuersuwan et al., 2008) and PM_2.5 in Malaysia (40.25 - 43.86 μg/m³), and a bit lower than PM₁₀ in Malaysia (101.83 - 102.47 μg/m³) (Azyan et al., 2018). However, those levels in EA could still acceptable since PM_2.5 and PM₁₀ average values were 26.21 ± 4.54 and 41.10 ± 4.96 μg/m³, respectively. Compare to other developed countries in Asia as Kanazawa, Suzu, and Saitama city in Japan (Hongtieab et al., 2020) the level of PM_2.5 and PM₁₀ in EA much higher. Nonetheless, as to the NAAQs of Indonesia, the level PM_2.5 and PM₁₀ limit for 24-hours in Padang city were still acceptable. Hereinafter, the range of PM₁ level in RA was varied from 23.23 - 33.29 μg/m³ which the mean level was 28.71 ± 3.84 μg/m³. Even there is no guideline for this particle size, it could be considered as a high concentration particularly in the RA site since it was still higher compared to the standard PM_2.5 standard from WHO.

Taking into account the ultrafine particle (PM_0.1) level, it is considered as the second-highest of PM mass concentration after PM_10-2.5 (see Figure 2(a)). The minimum, mean, and maximum of PM_0.1 in RA were 11.95, 14.56 ± 3.22, 19.08 μg/m³. It was comparable with the PM_0.1 in the roadside of Medan city (13.1 ± 3.8 μg/m³) (Putri et al., 2021) and a bit higher than PM_0.1 in Jambi city (9.2 - 9.6 μg/m³) (Amin et al., 2019), Sumatera Island, Indonesia. The high concentration of ultrafine particles could be emitted from the vehicle emission, fresh biomass burning nearby, and coal burning from the cement factory which will discuss in the following section.

The PM_0.1 ratio in various categories of PMs is listed in Table 1. PM_0.1/TSP was similar between sites, or, the mean PM_0.1/TSP was 0.19 ± 0.03 and 0.18 ± 0.02 respectively at RA and EA sites. Around a half of PM₁ in Padang city was considered as ultrafine particles (0.50 ± 0.06 at EA and 0.46 ± 0.03 in RA). It comparable with reported values in Japan (0.48 - 0.61) (Hongtieab et al., 2020). Since PM_2.5 is more familiar around the world compare to PM₁. PM_0.1 in our studies also compare to PM_2.5 and the mean ratio in the RA and EA was 0.34 ± 0.05 and 0.31 ± 0.02, which was quite similar to the ratio in Thailand (0.28) (Phairuang et al., 2019) and much higher than Vietnam (0.08 - 0.11) (Thuy et al., 2018) and Japan (0.15 - 0.21) (Hongtieab et al., 2020), suggested Padang city, Indonesia was more influenced by the smaller particles, particularly in the range of fine particles. It also can be seen from the ratio of PM₁/PM_2.5 and PM_2.5/PM₁₀ which much larger than 0.5 in both sites. However, a bit higher coarser fraction in RA compared to EA could be associated with the road dust or fly ash along the material transportation using trucks from the material sources to the cement factory.

Carbonaceous components represented the OC, EC, char-EC, soot-EC were shown in Table 2. The fraction OC and EC in both sites were comparable in all

particle sizes accounted 70.40 - 96.47; 3.53% - 29.60% and 72.75 - 97.06; 2.94% - 27.25% both at EA and RA, respectively. At both sites, fine fraction (2.5 - 1, 1 - 0.5, and <0.1 μm) were more enriched by EC than coarser fraction (2.5 - 10 and >10 μm). The total EC in fine-coarse in EA and RA was 1.37 - 0.86 μg/m³ and 1.40 - 0.98 μg/m³. It agreed with the previous studies by Guo (2016) which EC more abundance in fine particles since it commonly emitted from vehicle exhaust (Yang et al., 2019; Liu et al., 2020). However, the particle with size 2.5 - 10 mm contained the highest both OC and EC in all sites it might be due to the highest mass concentration among the particle sizes. The highest OC fraction was found in the particle with size 2.5 - 10 μm while for the EC, the higher fraction was founded in the particle 0.5 - 1 μm. As published by Phairuang et al. (2020) in Hat Yai, Thailand and Amin et al. (2019) in Sumatra, Indonesia, particles with the size 0.5 - 1 μm contained the highest EC among the other sizes.

The OC concentration in PM_0.1 varied from 2.54 to 5.06 μg/m³ and from 2.73 to 3.64 μg/m³ in EA and RA, respectively, notably higher than the concentration in developed countries at 0.10 to 0.14 μg/m³ and 0.18 μg/m³ for Los Angeles and Central Sacramento, USA respectively (Kuwayama et al., 2013; Xue et al., 2019). On the other hand, the level of EC in PM_0.1 mass concentration in both sites were similar (0.30 - 0.49 μg/m³ in EA and 0.30 - 0.51 μg/m³ in RA) which was higher than the previous study by Xue et al. (2019) in Los Angeles (0.03 - 0.05 μg/m³) and by Kuwayama et al. (2013) in Sacramento (0.06 μg/m³), USA. Furthermore, even compare to the value in Asian Countries, the EC concentration in PM_0.1 was still a bit higher than PM_0.1 EC in Hatyai city, Thailand (0.23 μg/m³) and Hanoi city, Vietnam (0.25 - 0.29 μg/m³), and Kanazawa, Suzu and Saitama city in Japan (0.07 - 0.18 μg/m³) (Thuy et al., 2018; Hongtieab et al., 2020; Phairuang et al., 2020).

The ratios OC/EC and char-EC/soot-EC are illustrated in Figure 3(a) and Figure 3(b) while the detail value was shown in Table 2. The average OC/EC ratio in all sizes for both sites was comparable since the distance between those two sites was not so far, for just around ±3.41 km (see Figure 1). The ratios OC/EC in PM_0.1 were varied from 2.54 to 5.06 and from 2.73 to 3.64 for EA and RA sites, respectively. The highest ratio of OC/EC in both sites was founded in PM_>10 for EA at 11.55 ± 6.67 and in PM_1-2.5 for RA sites at 11.57 ± 12.11. Overall, the ratio of OC/EC in Padang city in all sizes ranged from 2.38 to 32.98 indicated multiple types of emission sources contributed to both sites as motor vehicles exhaust, coal combustion, and biomass burning and might be attributed to the SOC since all sizes and days was exceeded 2.0 as an indicator of the presence of SOC (Guo, 2016).

Similar to the OC/EC ratio, char-EC/soot-EC ratio as the carbonaceous aerosol sources indicator are widely used even it could be more effective to use than OC/EC ratio since char-EC and soot-EC were not affected by SOC formation (Han et al., 2009). Based on the previous discussion, OC could be formed from SOC while EC only emitted from the primary emission. By using char-EC/soot-EC ratio as sources indicators, biased due to SOC could be ignored. As to these ratios, PM_0.1 char-EC/soot-EC ratio was the lowest compare to other particle sizes at 0.40 ± 0.27 and 0.39 ± 0.39 for EA and RA, respectively suggested that emission from diesel engines was the major contributor to the total EC concentrations (Han et al., 2016) in PM_0.1. Then, these two-carbon ratios in other particle sizes were increased particularly in the PM_>10 and PM_10-2.5 might be correlated to the presence of small-scale open biomass burning surrounding monitoring sites and the influenced of the cement industry that used coal as the main fuels. Published by Kumar and Atri (2016), biomass burning, and coal combustion emitted

an abundance of char-EC. For all particle sizes, the char-EC/soot-EC ratio in the EA site much larger than the RA site especially taking into account PM_10-2.5 which almost -3 times higher than RA. A lower char-EC/soot-EC ratio in RA for all particle sizes could be correlated to the sampling sites nearby the main street.

The correlation among carbonaceous component in PMs were shown in Table 3. There is no significant correlation between OC and EC in all particle sizes both in EA and RA except in the PM_>10 at EA (r = 0.93) and at RA (r = 0.96) sites, suggested OC and EC in both sizes were emitted from the typical sources. For further checking, the char-EC and soot-EC ratio also plotted together with the OC. In the same size of particles, i.e. PM_>10, a moderate and good correlation between char-EC and soot-EC with the OC were found in both sites. Not only in the PM_>10, even for all particle size, but also we found that soot-EC has a good correlation with OC in the RA sites, might be related to the emission from vehicles and the cement industry which high temperature applied as in the kiln process where the temperature could up to ±1450˚C. The same trend was found in the EA site where the soot-EC correlation with OC was more significant than the char-EC relationship with OC particularly in the fine and ultrafine sizes (Kim et al., 2011) suggested the emission from cement factory or roadside nearby were influenced EA site. In the PM_0.1, the negative and insignificant correlation between char-EC and soot-EC were found in both sites while for PM_>10, it showed a positive correlation with r value at 0.58 and 0.99 for EA and RA sites, respectively, indicated char-EC and soot-EC in ultrafine particles in both sites came from different sources.

To examine the effect of long-range transportation of aerosol particles to Padang city. Backward air mass trajectory to both sampling sites was discussed in this study and illustrated in Figure 4 regarding the air parcel movement, the air

mass came from the South China Sea passed through the neighboring province (Riau province). Riau province is one of the biggest contributors of aerosol particles since this province has a lot of peatland area which is very easy to burn particularly during dry season. However, since our samples were taken in the rainy season, biomass burning which represented by hotspot was not so important although it could not be ignored because the air mass that comes to sampling sites was passing through a small number of hotspots in Riau province. Then, the local emission as vehicle exhaust, coal burning together with biomass burning nearby sampling sites might be the main sources of the aerosol particle in both two sites.