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Phairuang, W.;  Piriyakarnsakul, S.;  Inerb, M.;  Hongtieab, S.;  Thongyen, T.;  Chomanee, J.;  Boongla, Y.;  Suriyawong, P.;  Samae, H.;  Chanonmuang, P.; et al. Ambient Nanoparticles Mapping in Thailand. Encyclopedia. Available online: https://encyclopedia.pub/entry/39953 (accessed on 16 November 2024).
Phairuang W,  Piriyakarnsakul S,  Inerb M,  Hongtieab S,  Thongyen T,  Chomanee J, et al. Ambient Nanoparticles Mapping in Thailand. Encyclopedia. Available at: https://encyclopedia.pub/entry/39953. Accessed November 16, 2024.
Phairuang, Worradorn, Suthida Piriyakarnsakul, Muanfun Inerb, Surapa Hongtieab, Thunyapat Thongyen, Jiraporn Chomanee, Yaowatat Boongla, Phuchiwan Suriyawong, Hisam Samae, Phuvasa Chanonmuang, et al. "Ambient Nanoparticles Mapping in Thailand" Encyclopedia, https://encyclopedia.pub/entry/39953 (accessed November 16, 2024).
Phairuang, W.,  Piriyakarnsakul, S.,  Inerb, M.,  Hongtieab, S.,  Thongyen, T.,  Chomanee, J.,  Boongla, Y.,  Suriyawong, P.,  Samae, H.,  Chanonmuang, P.,  Suwattiga, P.,  Chetiyanukornkul, T.,  Panyametheekul, S.,  Amin, M.,  Hata, M., & Furuuchi, M. (2023, January 10). Ambient Nanoparticles Mapping in Thailand. In Encyclopedia. https://encyclopedia.pub/entry/39953
Phairuang, Worradorn, et al. "Ambient Nanoparticles Mapping in Thailand." Encyclopedia. Web. 10 January, 2023.
Ambient Nanoparticles Mapping in Thailand
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This entry is adapted from the peer-reviewed paper 10.3390/atmos14010066

Nanoparticles (NPs), nanoaerosols (NAs), ultrafine particles (UFPs), and PM0.1 (diameters ≤ 0.1 µm or 100 nm) are used interchangeably in the field of atmospheric studies. PM0.1 mainly originate from combustion processes such as in motor vehicles. The highest mass concentration of PM0.1 occurs during the dry season, in which open fires occur in some regions of Thailand. The northern area of the country has higher PM0.1 mass concentrations, followed by the central and southern areas. Carbonaceous nanoaerosols are produced during normal periods, and the proportions of organic to elemental carbon and char to soot suggest that these originate from motor vehicles. However, in haze periods, biomass fires can also produce carbon-containing particles. PM0.1 pollution from local and cross-border countries also needs to be considered. The overall conclusions reached will likely have a beneficial long-term impact on achieving a blue sky over Thailand through the development of coherent policies and managing new air pollution challenges and sharing knowledge with a broader audience.

biomass burning motor vehicles nanoaerosols nanoparticles

1. Recent Studies of PM0.1 in Thailand

1.1. PM0.1 Particle Mass Concentration and Particle Number Concentration

The PM0.1 levels in ambient air are usually extensively measured by particle number concentration (PNC) due to their minuscule size in addition to mass concentration [1]. No standards for airborne PM0.1 have been adopted in Thailand. Thailand’s National Ambient Air Quality Standards recently established parameters for six air pollutants that are deemed the highest priority to protect public health, including PM (TSP, PM10, PM2.5), O3, CO, SO2, NO2, and lead (Pb). The six criteria for pollutants are classified into health risk levels based on criteria defined by Thailand’s Air Quality and Noise Management Bureau, Pollution Control Department, and Ministry of Natural Resources and Environment. This is the current standard as of 2022; particulate pollution is a severe and increasing problem for Thailand. The Pollution Control Department announced in 2022 [2] that it will decrease Thailand’s National Ambient Air Quality of 24 h PM2.5 concentration to 37.5 µg/m3 in 2023. This is because of human health concerns about smaller particles in the recent decade.
Moreover, according to the new guidelines on air quality by the World Health Organization (WHO) (2021) [3], the suggested mean annual concentration for PM10 was 200 µg/m3 in 2005 and the mass concentration for 2021 moved to 150 µg/m3. The 24 h concentration was updated from 50 µg/m3 in 2005 to 45 µg/m3. Furthermore, in 2005, the highest recommended average PM2.5 annual mass concentration was 10 µg/m3; the 2021 revision reduced that number by half, to just 5 µg/m3. The 24 h level changed from 25 µg/m3 in 2005 to 15 µg/m3. The WHO was confident that there was insufficient information to provide guidelines for other types of PM, including elemental and black carbon, sand and dust storm particles, and PM0.1 particles. The WHO does not create a set of best practices for managing those pollutants, even though it recommends further study into their risks and methods for mitigation.
In European countries, the Condensation Particle Counter (CPC) is a standard method for measuring nanoparticles [4]. However, the ambient nanoparticle standard for all emission types is still limited. Only the gasoline and diesel emission standard representing the non-volatile particle of diameter >23 nm has been defined (the Solid Particle Number > 23 nm method (SPN23)) [5]. Surface area and particle number are appropriate for measuring minor mass concentrations of PM0.1 in most atmospheres [6]. NPs are commonly measured as particle number concentration (PNC), representing more than 85% of the total PM2.5 particle number [7]. In contrast, it contributes only slightly (10–20%) to the total PM concentration.
In the BMR, the PM0.1/PM2.5 ratio is around 0.23 [8]. Motor vehicles account for smaller particles in this area, and the ratio slightly increases to 0.26 during the dry season, indicating that some biomass burning episodes produce PM0.1 [9]. Hat Yai, Songkhla province, is an economic city in the south of Thailand. A previous study showed that the primary particulate pollutants in Hat Yai are caused by biomass combustion from the rubber industry [10] because southern Thailand is different from the other regions of Thailand. The economic crop in the region is oil palm and para-rubber, which are produced in plantations in the south of Thailand [11][12]. However, PM0.1 in the southern part of Thailand is lower than in other parts due to less frequent open biomass burning fires in the area. The PM0.1/PM2.5 ranges from 0.15 to 0.19 depending on the transboundary particulate effects that increase the mass concentration [13][14].

1.2. Carbonaceous Nanoaerosol

The most significant portion of airborne PM is carbon-containing materials with various physical and chemical characteristics, which account for around 20–50% of the mass concentration of PMs [15][16]. The PM-bound total carbon (TC) can be divided into two types, including organic carbon (OC) and black carbon (BC) or elemental carbon (EC). BC and EC are used interchangeably depending on the analytical method being used [17][18]. Brown carbon (BrC) was recently discovered with light absorption characteristics similar to atmospheric aerosols [19]. BrC is a non-soot organic carbon aerosol that is produced from bioaerosols, tar, and humic-like substances (HULIS) [20][21]. BC is mainly emitted by high-temperature combustion processes (diesel and gasoline exhausts, coal combustion, and biomass burning) [22][23]. BrC is primarily emitted by biomass burning. BC and BrC are the two most crucial light-absorbing substances in atmospheric aerosols [24]. In contrast, OC is a light-scattering material that is mainly generated from biomass fires, coal combustion, motor vehicles, and secondary chemical processes in the atmosphere [25][26]. The Intergovernmental Panel on Climate Change (IPCC) predicted that EC would lead to a direct global radiative forcing of around +0.2 Wm−2 [27]. In contrast, OC was produced at around the same magnitude [28]. Therefore, the primary emissions of BC clearly have global warming potential and can influence the hydrological cycle [29]. Primary pollutants, including NOx, BC and OC, include an atmospheric photochemical activity and can produce secondary organic aerosols (SOA) and ozone (O3), creating an even more complicated effect [30].
Information concerning OC and EC is crucial in estimating the impact of PMs and the understanding of the source and strength of these pollutants. EC can be divided into char-EC and soot-EC [31]. Char consists of the residue remaining after burning solid residue. Soot, however, is different from the physical and chemical properties of the source materials after the high-temperature condensation of hot gases during the combustion process [32]. The ratio of Char-EC and Soot-EC varies depending on the main sources and can be used to categorize the origin of this material. Only a small number of studies have reported on the pattern for Thailand’s carbonaceous nanoaerosols (OC and EC) [8][9][14][33]. Brown carbon (BrC) in nanoaerosols, which affects the splitting between OC and EC via a thermal-optical protocol, has not been studied so far in Thailand. A reliable method for detecting BrC plays a vital role in accurately estimating carbonaceous nanoaerosols [34]. The effect on regional and global warming is highly uncertain due to carbonaceous aerosols that are emitted into the atmosphere. This is because the distribution of carbon fractions varies with the time and location, which basically contributes to the chemical, physical, and optical characteristics of carbon components in PMs. Accordingly, information on carbonaceous nanoaerosols is vital in terms of assessing their radiative effects on global warming. Only limited studies of carbon components and spatial and temporal variations in Thailand have appeared, particularly of the nano-scale ambient particles related to carbon components.

1.3. Carbon Characteristics of OC, EC, Char-EC, and Soot-EC

The ratios of OC/EC can be used to classify the exact emission sources of carbonaceous particulate matter. Ratios for diesel exhaust, coal burning, and biomass combustion are different. Biomass burning has a higher ratio, while the OC/EC ratios for fossil burning results are lower [35]. The ratio of OC to EC for biomass combustion is higher (~6–8) [36] and that from fossil fuel is lower (<1) [37]. The characteristics of emission sources of carbon fractions include diesel exhaust (OC/EC ~0.1–0.8) [26], biomass combustion (OC/EC ~4–6) [38][39], and long-range transport/aged aerosol (OC/EC ~12) [40]. On the other hand, OC/EC depends on three factors for appropriately categorizing the source of the emission. The three factors include the primary emission source, the deposition rate, and secondary organic aerosols (SOA) [14][26]. 
Unlike the OC/EC ratio, the char-EC/soot-EC ratio differs from each source; it is frequently possible to identify the sources [41]. Only two factors can affect the char/soot ratio: the primary emission source and particle deposition by scavenging. A higher proportion of char/soot (generally >1.0) is suggestive of biomass fires; char contributes to the total EC levels. In contrast, char/soot <1.0 suggests that emissions from diesel engines are an essential contributor to the total EC concentrations [8][42]. The Char-EC/Soot-EC ratios in nanoparticles in Thailand are almost constant and less than 1.0 in both the wet and dry seasons, suggesting that motor vehicles are a key source of PM0.1 particles in Thailand. However, only in Chiang Mai during the dry season, the Char-EC content and Char-EC/Soot-EC were increased higher than 1.0 because of open biomass burning to smaller particles [8][14][26]. Therefore, the PM0.1 particles represent diesel engine emissions, although sensitive to biomass emissions in Thailand, e.g., the Chiang Mai area, which is recognized to have airborne particulate pollution from biomass burning for a long time [43][44]. Moreover, the increased Char-EC content and Char-EC/Soot-EC ratio should be studied in detail in future studies for the accuracy of carbonaceous nanoaerosols in Thailand and elsewhere.

1.4. PM0.1 Derived from Biomass Burning

In SEA, haze has occurred nearly every year during the dry season [43][44]. These haze episodes generated PM that was derived from biomass combustion in the past decade [9][38]. Forest fires and slash and burn in agricultural areas are typical methods for removing biomass residues in SEA [45]. Research reports addressed the high PM concentration that is released from open biomass fires in Thailand [44][46][47]. Hata et al. (2014) [48] reported, based on chamber experiments, that biomass fuel combustion releases around 80% of all sub-micron particles and nanoparticles of approximately 30% of the total particles. Similarly, open biomass fires during a haze episode in northern Thailand revealed that more than 60% of the total PM is smaller than PM1.0 [8]. The size distribution of PM released from open fires depends on fuel type, moisture content, and excess air during combustion [49][50].
Biomass burning is a significant contributor to the production of ambient particles. As reported by Hata et al. (2014) [48], in chamber experiments, biomass solid fuel combustion accounted for more than 30% of the biomass burning and that the particle mass concentration was smaller than <100 nm. However, in the atmospheric environment, PM0.1 particles are contained in the ambient atmosphere due to anthropogenic activities and natural sources or chemical processes. Therefore, determining the actual emission sources under ambient conditions is not an easy task. Phairaung et al. (2021) [8] reported on the source apportionment of PM0.1 particles in Bangkok. They found that around 10% of the ambient nanoparticles in Bangkok during haze episodes came from biomass fires. However, PM0.1 particles, primarily derived from motor vehicle emissions, are also strongly affected by forest fires in the north of Thailand [8]. Hence, this activity has an important influence on the quality of ambient air during the dry season. As a result, the main emission sources of PM0.1 are both natural and anthropogenic.

2. Health Concerns of PM0.1 in Thailand

Smaller particles, especially nano-size particles, are recognized as being detrimental to human health due to their small size, chemical makeup, and the fact that they accumulate in ambient conditions [51]. Evidence collected in the past decade makes it clear that PM0.1 affects public health. The Health Effects Institute (HEI) [52] suggests that the PM0.1 data on health risk assessment are still an ongoing study and it cannot conclude or decide on policy making for the control of ambient PM0.1 worldwide. However, health risks, such as oxidative stress and inflammatory damage, may result from human exposure to atmospheric PM0.1 through inhalation [51][53].
In the same manner, studies of PM0.1 in Thailand make it clear that there are health effects from these particles. Only a few studies have appeared on health risk assessment from PM0.1 as related to the chemical composition of these particles. Chomanee et al. (2020) [13] reported on a health risk assessment of nanoparticle-bound PAHs in southern Thailand during a period of transboundary particulate pollution. It is known that the lower SEA suffers from the effects of large peat-land fires during the dry season, around July–September, almost every year.
Similarly, Phairuang et al. (2022) [54] reported on the year-long health effects of PM0.1-bound trace elements in southern Thailand in 2018. They found that the health risk from hazardous components is generally highly recognized during the pre-monsoon season. Toxic elements from peat-land fires that are transported from other sources to southern Thailand depend on the speed and direction of the wind. Cross-border particulate pollution must be investigated in more detail, with emphasis on the origin and health concerns during haze episodes in this region. During the normal period, the primary emission sources of PM0.1 are land transportation [33].
In other parts of Thailand, the knowledge of the health risks from PM0.1 related to the chemical components remains limited. Phairuang et al. (2021) [55] reported that the health risk assessment from PM0.1-bound metals in Bangkok, Thailand, was substantial during a smog haze period. PM0.1-bound elements in Bangkok differ with the season but are generally related to road transport emissions. It is well known that in the Bangkok Metropolitan Region air quality worsens during periods of heavy traffic congestion [8][56][57]. There is general agreement that the production of PM0.1 worldwide is derived from motor vehicles in urban areas [1][58]. Diesel and benzene engines are the primary sources of ambient nanoparticles in mega-cities [59][60]. However, open biomass burning, e.g., forest fires, crop waste, and grass burning, significantly contribute to PM0.1 during intense haze episodes in many countries [8][61]. Most studies have concluded that inhaled airborne PM0.1 has adverse effects on human health. Data of relationships between PM0.1 and sickness are limited.

3. Challenges in Studies of PM0.1 in Thailand

In the past decade, Thailand has been faced with particulate pollution almost yearly. In particular, in the dry season, emissions from open fires and meteorological conditions can temporarily affect the particle concentration [43][62]. Phairuang et al. (2019) [8] examined the influence of biomass fires on air quality in Thailand, i.e., Bangkok and Chiang Mai, in a case study of size-fractionated particulate matter ranging from small to nano-sized. The influence of biomass burning strongly affects ambient PM0.1 in Bangkok, although many reports have suggested that the main contribution of PM2.5 in BMR is from motor vehicles [56][57]. On the other hand, PM0.1 is ubiquitous in the atmospheric environment in the northern part of Thailand during the dry season, as in Chiang Mai, the economic city in the northern part of Thailand. This is a new challenge in the studies of biomass burning, especially crop waste burning and woodland fires in agricultural countries, to understand the production of ambient nanoparticles [8][14][61]. The apportionment of the sources of PM0.1 is very limited in Thailand due to the small amount of mass and chemical composition. Moreover, a recent study of particle size distribution in Bangkok by Panyametheekul et al. (2022) [63] found that the particle number concentration of samples collected from three locations in Bangkok revealed that up to 90% of the PM0.1 was produced in comparison with other sizes. Consequently, in the case of PM0.1, both the number and mass particle concentration are subjects that need to be examined in terms of air quality management in Thailand’s land based on heavy particulate pollution in the past decade.
It is generally assumed that PM0.1 particles are highly toxic substances compared to larger particles because they have a vast surface area per volume that can carry and absorb hazardous chemicals such as heavy metals, carbon components, and carcinogenic PAHs [51]. In the past decade, strong evidence has appeared to suggest that PM2.5 and PM10 induce human illness, including respiratory symptoms, cardiovascular effects, and chronic obstructive pulmonary disease (COPD), which contribute to mortality and morbidity [64][65][66][67]. This is especially true in northern Thailand, which experiences particulate pollution almost yearly. Many reports have revealed that the smoke haze episodes induce more people to visit hospitals in the north of Thailand [68][69]. However, there is no evidence of risks to health from nanoaerosols. Although the northern part of Thailand, during the dry season, has a high mass concentration of PM0.1 particles [8], the relationship and epidemiological survey of ultrafine particles and health effects still underestimate human public health due to insufficient information concerning the source, characteristics, and abundance of such small particles.

References

  1. De Jesus, A.L.; Rahman, M.M.; Mazaheri, M.; Thompson, H.; Knibbs, L.D.; Jeong, C.; Evans, G.; Nei, W.; Ding, A.; Qiao, L.; et al. Ultrafine particles and PM2.5 in the air of cities around the world: Are they representative of each other? Environ. Int. 2019, 129, 118–135.
  2. Pollution Control Department. National Thailand Ambient Air Quality Standards. 2022. Available online: https://www.pcd.go.th/laws/26439 (accessed on 1 December 2022).
  3. World Health Organization. WHO Global Air Quality Guidelines: Particulate Matter (PM2.5 and PM10), Ozone, Nitrogen Dioxide, Sulfur Dioxide and Carbon Monoxide. World Health Organization. 2021. Available online: https://apps.who.int/iris/handle/10665/345329 (accessed on 1 December 2022).
  4. CEN/TS 16976:2016; Ambient Air-Determination of the Particle Number Concentration of Atmospheric Aerosol. European Committee for Standardization: Brussels, Belgium, 2016.
  5. Giechaskiel, B.; Lahde, T.; Suarez-Bertoa, R.; Clairotte, M.; Grigoratos, T.; Zardini, A.; Perujo, A.; Martini, G. Particle number measurements in the European legislation and future JRC activities. Combust. Engines 2018, 174, 3–16.
  6. Chen, Q.; Wang, Q.; Xu, B.; Xu, Y.; Ding, Z.; Sun, H. Air pollution and cardiovascular mortality in Nanjing, China: Evidence highlighting the roles of cumulative exposure and mortality displacement. Chemosphere 2021, 265, 129035.
  7. Hinds, W.C.; Zhu, Y. Aerosol Technology: Properties, Behavior, and Measurement of Airborne Particles; John Wiley & Sons: Hoboken, NJ, USA, 2022.
  8. Phairuang, W.; Suwattiga, P.; Chetiyanukornkul, T.; Hongtieab, S.; Limpaseni, W.; Ikemori, F.; Hata, M.; Furuuchi, M. The influence of the open burning of agricultural biomass and forest fires in Thailand on the carbonaceous components in size-fractionated particles. Environ. Pollut. 2019, 247, 238–247.
  9. Boongla, Y.; Chanonmuang, P.; Hata, M.; Furuuchi, M.; Phairuang, W. The characteristics of carbonaceous particles down to the nanoparticle range in Rangsit city in the Bangkok Metropolitan Region, Thailand. Environ. Pollut. 2021, 272, 115940.
  10. Chomanee, J.; Tekasakul, S.; Tekasakul, P.; Furuuchi, M. Effect of irradiation energy and residence time on decomposition efficiency of polycyclic aromatic hydrocarbons (PAHs) from rubber wood combustion emission using soft X-rays. Chemosphere 2018, 210, 417–423.
  11. Office of Agricultural Economics (OAE). Agricultural Statistic in Thailand, 2019; OAE: Bangkok, Thailand, 2020.
  12. Phairuang, W.; Tekasakul, P.; Hata, M.; Tekasakul, S.; Chomanee, J.; Otani, Y.; Furuuchi, M. Estimation of air pollution from ribbed smoked sheet rubber in Thailand exports to Japan as a pre-product of tires. Atmos. Pollut. Res. 2019, 10, 642–650.
  13. Chomanee, J.; Thongboon, K.; Tekasakul, S.; Furuuchi, M.; Dejchanchaiwong, R.; Tekasakul, P. Physicochemical and toxicological characteristics of nanoparticles in aerosols in southern Thailand during recent haze episodes in lower southeast Asia. J. Environ. Sci. 2020, 94, 72–80.
  14. Phairuang, W.; Inerb, M.; Furuuchi, M.; Hata, M.; Tekasakul, S.; Tekasakul, P. Size-fractionated carbonaceous aerosols down to PM0.1 in southern Thailand: Local and long-range transport effects. Environ. Pollut. 2020, 260, 114031.
  15. Samiksha, S.; Kumar, S.; Sunder Raman, R. Two-year record of carbonaceous fraction in ambient PM2.5 over a forested location in central India: Temporal characteristics and estimation of secondary organic carbon. Air Qual. Atmos. Health 2021, 14, 473–480.
  16. Zioła, N.; Banasik, K.; Jabłońska, M.; Janeczek, J.; Błaszczak, B.; Klejnowski, K.; Mathews, B. Seasonality of the Airborne Ambient Soot Predominant Emission Sources Determined by Raman Microspectroscopy and Thermo-Optical Method. Atmosphere 2021, 12, 768.
  17. Rana, A.; Jia, S.; Sarkar, S. Black carbon aerosol in India: A comprehensive review of current status and future prospects. Atmos. Res. 2019, 218, 207–230.
  18. Zhang, Z.W.; Shahpoury, P.; Zhang, W.; Harner, T.; Huang, L. A new method for measuring airborne elemental carbon using PUF disk passive samplers. Chemosphere 2022, 299, 134323.
  19. Pani, S.K.; Lee, C.T.; Griffith, S.M.; Lin, N.H. Humic-like substances (HULIS) in springtime aerosols at a high-altitude background station in the western North Pacific: Source attribution, abundance, and light-absorption. Sci. Total Environ. 2022, 809, 151180.
  20. Tang, J.; Wang, J.; Zhong, G.; Jiang, H.; Mo, Y.; Zhang, B.; Geng, X.; Chen, Y.; Tang, J.; Tian, C.; et al. Measurement report: Long-emission-wavelength chromophores dominate the light absorption of brown carbon in aerosols over Bangkok: Impact from biomass burning. Atmos. Chem. Phys. 2021, 21, 11337–11352.
  21. Wonaschütz, A.; Hitzenberger, R.; Bauer, H.; Pouresmaeil, P.; Klatzer, B.; Caseiro, A.; Buxbaum, H. Application of the integrating sphere method to separate the contributions of brown and black carbon in atmospheric aerosols. Environ. Sci. Technol. 2009, 43, 1141–1146.
  22. Cui, M.; Xu, Y.; Yu, B.; Yan, C.; Li, J.; Zheng, M.; Chen, Y. Experimental simulation characterizes carbonaceous matter emitted from residential coal and biomass combustion. Atmos. Environ. 2023, 293, 119447.
  23. Malmborg, V.; Eriksson, A.; Gren, L.; Török, S.; Shamun, S.; Novakovic, M.; Zhang, Y.; Kook, S.; Tunér, M.; Bengtsson, P.-E.; et al. Characteristics of BrC and BC emissions from controlled diffusion flame and diesel engine combustion. Aerosol Sci. Technol. 2021, 55, 769–784.
  24. Runa, F.; Islam, M.; Jeba, F.; Salam, A. Light absorption properties of brown carbon from biomass burning emissions. Environ. Sci. Pollut. Res. 2022, 29, 21012–21022.
  25. Hallquist, M.; Wenger, J.C.; Baltensperger, U.; Rudich, Y.; Simpson, D.; Claeys, M.; Dommen, J.; Donahue, N.M.; George, C.; Goldstein, A.H.; et al. The formation, properties, and impact of secondary organic aerosol: Current and emerging issues. Atmos. Chem. Phys. 2009, 9, 5155–5236.
  26. Amin, M.; Handika, R.A.; Putri, R.M.; Phairuang, W.; Hata, M.; Tekasakul, P.; Furuuchi, M. Size-segregated particulate mass and carbonaceous components in roadside and riverside environments. Appl. Sci. 2021, 11, 10214.
  27. Houghton, J.T.; Ding, Y.D.J.G.; Griggs, D.J.; Noguer, M.; van der Linden, P.J.; Dai, X.; Maskell, K.; Johnson, C.A. (Eds.) Climate Change 2001: The Scientific Basis: Contribution of Working Group I to the Third Assessment Report of the Intergovernmental Panel on Climate Change; Cambridge University Press: Cambridge, UK, 2001.
  28. Kelesidis, G.A.; Bruun, C.A.; Pratsinis, S.E. The impact of organic carbon on soot light absorption. Carbon 2021, 172, 742–749.
  29. Gustafsson, Ö.; Ramanathan, V. Convergence on climate warming by black carbon aerosols. Proc. Natl. Acad. Sci. USA 2016, 113, 4243–4245.
  30. Irei, S.; Takami, A.; Sadanaga, Y.; Nozoe, S.; Yonemura, S.; Bandow, H.; Yokouchi, Y. Photochemical age of air pollutants, ozone, and secondary organic aerosol in transboundary air observed on Fukue Island, Nagasaki, Japan. Atmos. Chem. Phys. 2016, 16, 4555–4568.
  31. Han, Y.; Chen, Y.; Feng, Y.; Shang, Y.; Li, J.; Li, Q.; Chen, J. Existence and formation pathways of high-and low-maturity elemental carbon from solid fuel combustion by a time-resolved study. Environ. Sci. Technol. 2022, 56, 2551–2561.
  32. Falk, J.; Korhonen, K.; Malmborg, V.B.; Gren, L.; Eriksson, A.C.; Karjalainen, P.; Markkula, L.; Bengtsson, P.-E.; Virtanen, A.; Svenningsson, B.; et al. Immersion freezing ability of freshly emitted soot with various physico-chemical characteristics. Atmosphere 2021, 12, 1173.
  33. Inerb, M.; Phairuang, W.; Paluang, P.; Hata, M.; Furuuchi, M.; Wangpakapattanawong, P. Carbon and Trace Element Compositions of Total Suspended Particles (TSP) and Nanoparticles (PM0.1) in Ambient Air of Southern Thailand and Characterization of Their Sources. Atmosphere 2022, 13, 626.
  34. Zhang, Y.; Peng, Y.; Song, W.; Zhang, Y.L.; Ponsawansong, P.; Prapamontol, T.; Wang, Y. Contribution of brown carbon to the light absorption and radiative effect of carbonaceous aerosols from biomass burning emissions in Chiang Mai, Thailand. Atmos. Environ. 2021, 260, 118544.
  35. Singh, G.K.; Choudhary, V.; Rajeev, P.; Paul, D.; Gupta, T. Understanding the origin of carbonaceous aerosols during periods of extensive biomass burning in northern India. Environ. Pollut. 2021, 270, 116082.
  36. Tao, J.; Zhang, Z.; Zhang, L.; Huang, D.; Wu, Y. Quantifying the relative importance of major tracers for fine particles released from biofuel combustion in households in the rural North China Plain. Environ. Pollut. 2021, 268, 115764.
  37. Yang, H.H.; Dhital, N.B.; Wang, L.C.; Hsieh, Y.S.; Lee, K.T.; Hsu, Y.T.; Huang, S.C. Chemical characterization of fine particulate matter in gasoline and diesel vehicle exhaust. Aerosol Air Qual. Res. 2019, 19, 1349–1449.
  38. Adam, M.G.; Tran, P.T.; Bolan, N.; Balasubramanian, R. Biomass burning-derived airborne particulate matter in Southeast Asia: A critical review. J. Hazard. Mater. 2021, 407, 124760.
  39. Thumanu, K.; Pongpiachan, S.; Ho, K.F.; Lee, S.C.; Sompongchaiyakul, P. Characterization of organic functional groups, water-soluble ionic species and carbonaceous compounds in PM10 from various emission sources in Songkhla Province, Thailand. WIT Trans. Ecol. Environ. 2009, 123, 295–306.
  40. Saarikoski, S.; Timonen, H.; Saarnio, K.; Aurela, M.; Järvi, L.; Keronen, P.; Kerminen, V.-M.; Hillamo, R. Sources of organic carbon in fine particulate matter in northern European urban air. Atmos. Chem. Phys. 2008, 8, 6281–6295.
  41. Guo, Y. Carbonaceous aerosol composition over northern China in spring 2012. Environ. Sci. Pollut. Res. 2015, 22, 10839–10849.
  42. Han, Y.M.; Chen, L.W.; Huang, R.J.; Chow, J.C.; Watson, J.G.; Ni, H.Y.; Liu, S.X.; Fung, K.K.; Shen, Z.X.; Wei, C.; et al. Carbonaceous aerosols in megacity Xi’an, China: Implications for comparison of thermal/optical protocols. Atmos. Environ. 2016, 132, 58–68.
  43. Moran, J.; Nasuwan, C.; Poocharoen, O.O. A review of the haze problem in Northern Thailand and policies to combat it. Environ. Sci. Policy 2019, 97, 1–15.
  44. Phairuang, W.; Hata, M.; Furuuchi, M. Influence of agricultural activities, forest fires and agro-industries on air quality in Thailand. J. Environ. Sci. 2017, 52, 85–97.
  45. Janta, R.; Sekiguchi, K.; Yamaguchi, R.; Sopajaree, K.; Plubin, B.; Chetiyanukornkul, T. Spatial and temporal variations of atmospheric PM10 and air pollutants concentration in upper Northern Thailand during 2006–2016. Appl. Sci. Eng. Prog. 2020, 13, 256–267.
  46. Punsompong, P.; Pani, S.K.; Wang, S.H.; Pham, T.T.B. Assessment of biomass-burning types and transport over Thailand and the associated health risks. Atmos. Environ. 2021, 247, 118176.
  47. Vongruang, P.; Pimonsree, S. Biomass burning sources and their contributions to PM10 concentrations over countries in mainland Southeast Asia during a smog episode. Atmos. Environ. 2020, 228, 117414.
  48. Hata, M.; Chomanee, J.; Thongyen, T.; Bao, L.; Tekasakul, S.; Tekasakul, P.; Otani, Y.; Furuuchi, M. Characteristics of nanoparticles emitted from burning of biomass fuels. J. Environ. Sci. 2014, 26, 1913–1920.
  49. Samae, H.; Tekasakul, S.; Tekasakul, P.; Furuuchi, M. Emission factors of ultrafine particulate matter (PM < 0.1 μm) and particle-bound polycyclic aromatic hydrocarbons from biomass combustion for source apportionment. Chemosphere 2021, 262, 127846.
  50. Samae, H.; Tekasakul, S.; Tekasakul, P.; Phairuang, W.; Furuuchi, M.; Hongtieab, S. Particle-bound organic and elemental carbons for source identification of PM< 0.1 µm from biomass combustion. J. Environ. Sci. 2022, 113, 385–393.
  51. Schraufnagel, D.E. The health effects of ultrafine particles. Exp. Mol. Med. 2020, 52, 311–317.
  52. HEI. Understanding the health effects of ambient ultrafine particles. In HEI Perspectives HEI Review Panel on Ultrafine Particles; Health Effects Institute: Boston, MA, USA, 2013.
  53. Kwon, H.S.; Ryu, M.H.; Carlsten, C. Ultrafine particles: Unique physicochemical properties relevant to health and disease. Exp. Mol. Med. 2020, 52, 318–328.
  54. Phairuang, W.; Inerb, M.; Hata, M.; Furuuchi, M. Characteristics of trace elements bound to ambient nanoparticles (PM0.1) and a health risk assessment in southern Thailand. J. Hazard. Mater. 2022, 425, 127986.
  55. Phairuang, W.; Suwattiga, P.; Hongtieab, S.; Inerb, M.; Furuuchi, M.; Hata, M. Characteristics, sources, and health risks of ambient nanoparticles (PM0.1) bound metal in Bangkok, Thailand. Atmos. Environ. X 2021, 12, 100141.
  56. ChooChuay, C.; Pongpiachan, S.; Tipmanee, D.; Suttinun, O.; Deelaman, W.; Wang, Q.; Xing, L.; Li, G.; Han, Y.; Palakun, J.; et al. Impacts of PM2.5 sources on variations in particulate chemical compounds in ambient air of Bangkok, Thailand. Atmos. Pollut. Res. 2020, 11, 1657–1667.
  57. Narita, D.; Oanh, N.; Sato, K.; Huo, M.; Permadi, D.; Chi, N.; Ratanajaratroj, T.; Pawarmart, I. Pollution characteristics and policy actions on fine particulate matter in a growing Asian economy: The case of Bangkok Metropolitan Region. Atmosphere 2019, 10, 227.
  58. Ding, X.; Kong, L.; Du, C.; Zhanzakova, A.; Wang, L.; Fu, H.; Chen, J.; Yang, X.; Cheng, T. Long-range and regional transported size-resolved atmospheric aerosols during summertime in urban Shanghai. Sci. Total Environ. 2017, 583, 334–343.
  59. Kumar, P.; Morawska, L.; Birmili, W.; Paasonen, P.; Hu, M.; Kulmala, M.; Harrison, R.M.; Norford, L.; Britter, R. Ultrafine particles in cities. Environ. Int. 2014, 66, 1–10.
  60. Kumar, P.; Pirjola, L.; Ketzel, M.; Harrison, R.M. Nanoparticle emissions from 11 non-vehicle exhaust sources–a review. Atmos. Environ. 2013, 67, 252–277.
  61. Thuy, N.T.T.; Dung, N.T.; Sekiguchi, K.; Thuy, L.B.; Hien, N.T.T.; Yamaguchi, R. Mass concentrations and carbonaceous compositions of PM0.1, PM2.5, and PM10 at Hanoi, Vietnam urban locations. Aerosol Air Qual. Res. 2018, 18, 1591–1605.
  62. Kliengchuay, W.; Worakhunpiset, S.; Limpanont, Y.; Meeyai, A.C.; Tantrakarnapa, K. Influence of the meteorological conditions and some pollutants on PM10 concentrations in Lamphun, Thailand. J. Environ. Health Sci. Eng. 2021, 19, 237–249.
  63. Panyametheekul, S.; Kangwansupamonkon, W.; Anuchitchanchai, O.; Pongkiatkul, P. Final Report “Research Program on Integrated Technology for Mitigating PM2.5: A Case Study in Bangkok Metropolitan Region (BMR)”. National Research Council Fund. 2022. Available online: https://scholar.google.com/citations?view_op=view_citation&hl=en&user=Eb81oY0AAAAJ&sortby=pubdate&citation_for_view=Eb81oY0AAAAJ:4OULZ7Gr8RgC (accessed on 1 December 2022).
  64. Ahmad, M.; Manjantrarat, T.; Rattanawongsa, W.; Muensri, P.; Saenmuangchin, R.; Klamchuen, A.; Aueviriyavit, S.; Sukrak, K.; Kangwansupamonkon, W.; Panyametheekul, S. Chemical Composition, Sources, and Health Risk Assessment of PM2.5 and PM10 in Urban Sites of Bangkok, Thailand. Int. J. Environ. Res. Public Health 2022, 19, 14281.
  65. Fold, N.R.; Allison, M.R.; Wood, B.C.; Thao, P.T.; Bonnet, S.; Garivait, S.; Kamens, R.; Pengjan, S. An assessment of annual mortality attributable to ambient PM2.5 in Bangkok, Thailand. Int. J. Environ. Res. Public Health 2020, 17, 7298.
  66. Pothirat, C.; Chaiwong, W.; Liwsrisakun, C.; Bumroongkit, C.; Deesomchok, A.; Theerakittikul, T.; Limsukon, A.; Tajarernmuang, P.; Phetsuk, N. The short-term associations of particular matters on non-accidental mortality and causes of death in Chiang Mai, Thailand: A time series analysis study between 2016–2018. Int. J. Environ. Health Res. 2021, 31, 538–547.
  67. Thao, N.N.L.; Pimonsree, S.; Prueksakorn, K.; Thao, P.T.B.; Vongruang, P. Public health and economic impact assessment of PM2.5 from open biomass burning over countries in mainland Southeast Asia during the smog episode. Atmos. Pollut. Res. 2022, 13, 101418.
  68. Uttajug, A.; Ueda, K.; Oyoshi, K.; Honda, A.; Takano, H. Association between PM10 from vegetation fire events and hospital visits by children in upper northern Thailand. Sci. Total Environ. 2021, 764, 142923.
  69. Uttajug, A.; Ueda, K.; Seposo, X.T.; Honda, A.; Takano, H. Effect of a vegetation fire event ban on hospital visits for respiratory diseases in Upper Northern Thailand. Int. J. Epidemiol. 2022, 51, 514–524.
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Subjects: Meteorology & Atmospheric Sciences
Contributors MDPI registered users' name will be linked to their SciProfiles pages. To register with us, please refer to https://encyclopedia.pub/register :
Worradorn Phairuang
,
Suthida Piriyakarnsakul
,
Muanfun Inerb
,
Surapa Hongtieab
,
Thunyapat Thongyen
,
Jiraporn Chomanee
,
Yaowatat Boongla
,
Phuchiwan Suriyawong
,
Hisam Samae
,
Phuvasa Chanonmuang
,
Panwadee Suwattiga
,
Thaneeya Chetiyanukornkul
,
Sirima Panyametheekul
,
Muhammad Amin
,
Mitsuhiko Hata
,
Masami Furuuchi
View Times: 440
Revisions: 3 times (View History)
Update Date: 11 Jan 2023
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