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Zhang, Y.; Guo, Z.; Zhuo, L.; An, N.; Han, Y. Highly Occupied Public Environments. Encyclopedia. Available online: (accessed on 20 June 2024).
Zhang Y, Guo Z, Zhuo L, An N, Han Y. Highly Occupied Public Environments. Encyclopedia. Available at: Accessed June 20, 2024.
Zhang, Yongzhi, Zengrui Guo, Lanting Zhuo, Nirui An, Yifei Han. "Highly Occupied Public Environments" Encyclopedia, (accessed June 20, 2024).
Zhang, Y., Guo, Z., Zhuo, L., An, N., & Han, Y. (2023, July 14). Highly Occupied Public Environments. In Encyclopedia.
Zhang, Yongzhi, et al. "Highly Occupied Public Environments." Encyclopedia. Web. 14 July, 2023.
Highly Occupied Public Environments

A minimum of 30 m3/h per person is required in common environments. Highly occupied public environments gather a large number of people in some time periods, and an air supply of 20–30 m3/h per person is needed. In addition, the highly occupied public environments have larger spaces, the personnel activities are more complex, and the social distance is shorter. Personnel activities may increase the pollutant transmission distance. During the COVID-19 pandemic, public safety in crowded places became a great concern.

crowded places ventilation strategies highly occupied public environments socially distance pollutants

1. Introduction

With economic development and urban expansion, people’s commuting distances are increasing, so the time spent on public transportation is increasing. The expansion of global air travel has overcome geographic barriers to disease vectors [1]. Passenger health is influenced by the cabin environment [2]. Airplane cabins provide a conducive environment for the transmission of COVID-19 [3]. Crowded economy-class cabin seats increase the risk of airborne disease transmission between sick and healthy passengers [4]. Of particular note is the emergence of COVID-19, which is transmitted mainly through droplets and aerosols [5][6]. Due to the high occupant density in an airplane cabin, the required total air exchange ratio is much higher than that in a building.
In typical offices, outdoor particulate matter <2.5 µm (PM 2.5) is the main source of indoor PM 2.5 [7]. Sangiorgi et al. reported that more than 80% of indoor PM 2.5 in office buildings comes from outdoors [8]. Mechanical ventilation filtration systems in office buildings are used to reduce indoor particulate matter exposure [9]. In the United States and Singapore, 90% of the indoor air in office buildings is recycled and filtered [10]. In China, a small number of office buildings directly use fresh air systems to provide filtered fresh air [11]. Previous research has found that crowded classrooms, apart from PM 2.5, are also associated with high levels of several chemicals, such as methanol and benzene [12][13]. Moreover, poor ventilation rates may lead to high levels of fungal particles in overcrowded places. Researchers have found that CO and PM levels were positively associated with students’ absence rates [14][15]. Indoor pollutants, including particulate pollutants, can affect student attendance and learning efficiency [16][17]. Many research teams have measured the concentration of pollutants in the classroom, and natural ventilation by opening windows is the main method [18][19]. A significant decrease in CO was found, which led to a reduction in respiratory illnesses in students [20]. But that would only be correct if the windows were actually opened and not left closed (to conserve heat). In addition to CO, NO2 emitted by motor vehicles in inner cities may cause excess morbidity, especially related to asthma symptoms [21]. The levels of various pollutants were found to be higher indoors than outdoors [22]. Additionally, suggestive evidence links the classroom-level ventilation rate with students’ test results in math [17][23]. Therefore, the health of occupants is extremely susceptible to the influence of outdoor pollutants, and due to the crowded nature of classrooms, the contaminants cause higher levels of exposure for occupants.
The effectiveness of filtration systems for PM 2.5 purification in the area of human activity and therefore respiration has received widespread attention. The PM produced by commercial aircraft not only has a significant impact on the outdoor environment of terminal buildings [24], but also easily transfers from outdoors to indoors through mechanical ventilation systems [25].
The literature on airborne transmission for different modes of transportation and transportation hubs is relatively limited. Due to their unique physical structure and high passenger flow within the transportation infrastructure, subway lines have a high risk of epidemic transmission [26][27]. The CO2 level was found to be linearly related to the number of passengers according to a correlation analysis [28]. It is important to consider commuter route choice in exposure assessment studies. The external environment has the strongest influence on air quality in subway cabins. The piston wind from the tunnel makes it easier to transport particulate matter into a subway station for a subway without platform screen doors.

2. Overview of Highly Occupied Public Environments

A minimum of 30 m3/h per person is required in common environments. Highly occupied public environments gather a large number of people in some time periods, and an air supply of 20–30 m3/h per person is needed. In addition, the highly occupied public environments have larger spaces, the personnel activities are more complex, and the social distance is shorter. Personnel activities may increase the pollutant transmission distance. During the COVID-19 pandemic, public safety in crowded places became a great concern.
People’s work and studies are closely related to densely crowded environments, as shown in Figure 1. Means of transportation are usually boarded in transportation hubs, which contain dense and highly mobile populations. This complex environment increases the risk of personal exposure. Commuters can easily carry viruses and bacteria from transportation hubs to public transportation, where crowds are dense and the social distance is short, which increases the risk of cross-infection. Finally, controlling the level of pollutants and reducing the risk of personal exposure in the air environment of densely crowded spaces such as classrooms and offices is urgently needed.
Figure 1. Structure of highly occupied public environment.
The relevant review articles on pollutant exposure in highly occupied public environments are shown in Table 1. Droplets are large heavy particles that transfer from person to person in close proximity and are the main reason for the need to socially distance (say 1–2 m). They usually fall to the ground. The other main and more insidious mode of transfer of virus particles is small and lighter-weight aerosols that can drift within enclosed interior spaces of airflow and cause infection to others.
Table 1. Summary of review articles about pollutant exposure in highly occupied public environments.
Classification Highly Occupied Public Environments Research Object Main Conclusions
Crowded places Classroom NO2, O3, PM, VOCs, bacteria Occupancy activities caused a large fraction of virus transmission due to the resuspension of previously deposited matter [29].
Hospitals, Schools, Offices Infectious diseases Ventilation is positively associated with airflow direction control in buildings [30].
Homes, Schools, and Hospitals Humidity, influenza virus, VOCs Humidity and temperature can be adjusted to achieve a satisfactory work environment [31].
Public Spaces Aerosol The range of typical indoor aerosols can be used as a reference for biosensors designed to improve public safety [32].
Public transport Pedestrians, Car, Bus, Massive Motorized Transport Black carbon, carbon monoxide, coarse particles, fine particles, NO2 Pedestrians have higher levels of inhaled pollutants than commuters using motor cabins [33].
Taxi, Bus, Subway, Busy Street PM, CO, NO2, volatile organic compounds (VOCs), polycyclic aromatic hydrocarbons (PAHs) There are differences in measurement methods and a lack of uniform measurement standards [34].
Walk, Cycle, Car, and Bus PM 2.5, ultrafine particles (UFPs), and black carbon The concentrations of PM 2.5, ultrafine particles (UFPs), and black carbon (BC) in Asian cities are higher than those in the USA and Europe [35].
Cycle, Car, Subway, and Bus PM, BC The levels of a bus passenger’s exposure to PM and BC largely depend on the bus route chosen [36].
Walk, Bicycle, Car, Bus PM 2.5, BC, UFPs, CO Car drivers are exposed more than pedestrians [37].
Walking, Cycling, Bus, Car, and Taxi PM 2.5, BC, UFPs, CO Pedestrians are exposed to lower levels of UFPs and CO than people inside vehicles [38].
Bicycle, Bus, Automobile, Rail, Walking, and Ferry Modes UFPs Exposure to UFPs can have acute effects on health-compromised individuals [39].
Subway PM Underground PM is more toxic than urban PM [40].
Subway PM The dust in a subway system is more toxic than ambient airborne particulates [41].
Subway CO, PMs, VOCs The ventilation mode, passenger numbers, and surrounding pollution level outside of a metro station could have important effects on the metro air quality [42].
Aircraft Airborne expiratory contaminants Most researchers have applied Lagrangian models to analyze transient phenomena [43].
Aircraft Droplets, SARS Most diseases have an incubation period that is longer than the period of air travel [44].
Transport hub Transportation and Transportation Hubs Respiratory viruses Air transportation appears to be important for accelerating influenza propagation [45].
Subway Stations High temperature, high humidity, PM, VOCs Ventilation can spread air pollutants through a complex airflow [46].
This study Classroom, Office, Subway station, Airport, Bus, Subway, Aircraft CO, PM, droplets The pollutant concentration detection system should be combined with the air-conditioning system in crowded places.
Passenger flow had a great influence on pollutant transport in transport hubs.
The average concentrations of PM 2.5 and total suspended PM that people taking subways are exposed to are 8 and 12 times those to which taxi drivers are exposed, respectively [41]. Moreover, uniform measurement standards are rarely applied to Asia [34][35]. Future work should place an emphasis on confirming the contribution of ultrafine particle (UFP) exposure to total PM exposure during transportation [39]. Exhaled droplets are transmitted in indoor environments, either directly or through air distribution [47]. PM, black carbon (BC), CO, fungal particles, bacteria, and viruses are frequently the main pollutants identified in subways.
Occupant density and occupant activities have a high impact on indoor air quality. The level of indoor aerosols is mainly affected by indoor population density, outdoor air level, and ventilation type [48]. Considering the coupled relationship between the indoor environment and ventilation, internal ventilation strategies should be determined according to outdoor conditions [46]. Currently, there are insufficient data to assess the relationship between the ventilation rates of highly occupied public environments and airborne infectious diseases, and there is a lack of quantitative research on the impact of occupant activities on pollutant transmission. Therefore, future work should focus on investigating the health risks posed by air pollutants and further developing advanced ventilation strategies to improve air quality in crowded places. The main indoor air pollutants in classrooms include viruses, PM, and volatile organic compounds (VOCs).
Poor ventilation and crowding are environmental factors that affect the risk of airborne infection in ground public transportation [49][50]. In the absence of sufficient air renewal, high transmission of influenza may occur in confined spaces. Therefore, the concentration in underground or closed stations may be several times higher than the concentration in the surrounding air [51][52][53]. Due to the metal wear of wheels and brake shoes in subway tunnels, the level of Fe-containing particles and black carbon level (PM, BC) are high in subway stations [54][55][56][57].


  1. Tatem, A.J.; Hay, S.I.; Rogers, D.J. Global traffic and disease vector dispersal. Proc. Natl. Acad. Sci. USA 2006, 103, 6242–6247.
  2. Hinninghofen, H.; Enck, P. Passenger well-being in airplanes. Auton. Neurosci. Basic Clin. 2006, 129, 80–85.
  3. Wang, C.; Horby, P.; Hayden, F.G.; Gao, G.F. A novel coronavirus outbreak of global health concern. Lancet 2020, 395, 470–473.
  4. Karlsson, H.L.; Nilsson, L.; Moller, L. Subway particles are more genotoxic than street particles and induce oxidative stress in cultured human lung cells. Chem. Res. Toxicol. 2005, 18, 19–23.
  5. Nakamura, H.; Managi, S. Airport risk of importation and exportation of the COVID-19 pandemic. Transp. Policy 2020, 96, 40–47.
  6. Dai, H.; Zhao, B. Association of the infection probability of COVID-19 with ventilation rates in confined spaces. Build. Simul. 2020, 13, 1321–1327.
  7. Quang, T.N.; He, C.; Morawska, L.; Knibbs, L.D. Influence of ventilation and filtration on indoor particle concentrations in urban office buildings—ScienceDirect. Atmos. Environ. 2013, 79, 41–52.
  8. Sangiorgi, G.; Ferrero, L.; Ferrini, B.S.; Porto, C.L.; Perrone, M.G.; Zangrando, R.; Gambaro, A.; Lazzati, Z.; Bolzacchini, E. Indoor airborne particle sources and semi-volatile partitioning effect of outdoor fine PM in offices. Atmos. Environ. 2013, 65, 205–214.
  9. Hanley, J.T.; Ensor, D.S.; Smith, D.D.; Sparks, L.E. Fractional Aerosol Filtration Efficiency of In-Duct Ventilation Air Cleaners. Indoor Air 2010, 4, 169–178.
  10. Zuraimi, M.S.; Tham, K.W. Reducing particle exposures in a tropical office building using electrostatic precipitators. Build. Environ. 2009, 44, 2475–2485.
  11. Ren, J.; Liu, J.; Cao, X.; Hou, Y. Influencing factors and energy-saving control strategies for indoor fine particles in commercial office buildings in six Chinese cities. Energy Build. 2017, 149, 171–179.
  12. Canha, N.; Martinho, M.; Almeida-Silva, M.; Freitas, M.d.C.; Almeida, S.M.; Pegas, P.; Alves, C.l.; Pio, C.; Trancoso, M.A.; Sousa, R.; et al. Indoor air quality in primary schools. Int. J. Environ. Pollut. 2012, 50, 396–410.
  13. Pegas, P.; Evtyugina, M.; Alves, C.l.; Nunes, T.; Cerqueira, M.r.; Franchi, M.; Pio, C.; Susana, P.; Almeida, S.; Do, M.; et al. Outdoor/indoor air quality in primary schools in Lisbon: A preeliminary study. Quim. Nova 2010, 33, 1145–1149.
  14. Currie, J.; Hanushek, E.A.; Kahn, E.M.; Neidell, M.; Rivkin, S.G. Does Pollution Increase School Absences? Rev. Econ. Stat. 2009, 91, 682–694.
  15. Geiss, O.; Barrero-Moreno, J.; Tirendi, S.; Kotzias, D. Exposure to Particulate Matter in Vehicle Cabins of Private Cars. Aerosol Air Qual. Res. 2010, 10, 581–588.
  16. Twardella, D.; Matzen, W.; Lahrz, T.; Burghardt, R.; Spegel, H.; Hendrowarsito, L.; Frenzel, A.C.; Fromme, H.; Twardella, D. Effect of classroom air quality on students’ concentration: Results of a cluster-randomized cross-over experimental study. Indoor Air 2012, 22, 378–387.
  17. Shaughnessy, R.J.; Haverinen-Shaughnessy, U.; Nevalainen, A.; Moschandreas, D. A preliminary study on the association between ventilation rates in classrooms and student performance. Indoor Air 2010, 16, 465–468.
  18. Blondeau, P.; Iordache, V.; Poupard, O.; Genin, D.; Allard, F. Relationship between outdoor and indoor air quality in eight French schools. Indoor Air 2010, 15, 2–12.
  19. Almeida, S.M.; Canha, N.; Silva, A.; do Carmo Freitas, M.; Pegas, P.; Alves, C.; Evtyugina, M.; Pio, C.A. Children exposure to atmospheric particles in indoor of Lisbon primary schools. Atmos. Environ. 2011, 45, 7594–7599.
  20. Estrella, B.; Sempértegui, F.; Franco, O.H.; Cepeda, M.; Naumova, E.N. Air pollution control and the occurrence of acute respiratory illness in school children of Quito, Ecuador. J. Public Health Policy 2018, 40, 17–34.
  21. O’Connor, G.T.; Neas, L.; Vaughn, B.; Kattan, M.; Mitchell, H.; Crain, E.F.; Evans, R.; Gruchalla, R.; Morgan, W.; Stout, J.; et al. Acute respiratory health effects of air pollution on children with asthma in US inner cities. J. Allergy Clin. Immunol. 2008, 121, 1133–1139.e1131.
  22. Shree, V.; Marwaha, B.; Awasthi, P. Indoor Air Quality Investigation at Primary Classrooms in Hamirpur, Himachal Pradesh, India. Hydro Nepal J. Water Energy Environ. 2019, 24, 45–48.
  23. Heracleous, C.; Michael, A. Experimental assessment of the impact of natural ventilation on indoor air quality and thermal comfort conditions of educational buildings in the Eastern Mediterranean region during the heating period. J. Build. Eng. 2019, 26, 100917.
  24. Mazaheri, M.; Johnson, G.R.; Morawska, L. Particle and gaseous emissions from commercial aircraft at each stage of the landing and takeoff cycle. Environ. Sci. Technol. 2009, 43, 441–446.
  25. Massey, D.; Kulshrestha, A.; Masih, J.; Taneja, A. Seasonal trends of PM10, PM5.0, PM 2.5 & PM1.0 in indoor and outdoor environments of residential homes located in North-Central India. Build. Environ. 2012, 47, 223–231.
  26. Troko, J.; Myles, P.R.; Gibson, J.E.; Hashim, A.; Enstone, J.E.; Kingdon, S.; Packham, C.; Amin, S.; Hayward, A.; Vantam, J. Is public transport a risk factor for acute respiratory infection. BMC Infect. Dis. 2011, 11, 16.
  27. Zhao, B.; Ni, S.; Yong, N.; Ma, X.; Ji, X. A Preliminary Study on Spatial Spread Risk of Epidemics by Analyzing the Urban Subway Mobility Data. J. Biosci. Med. 2015, 3, 15–21.
  28. Kwon, S.B.; Cho, Y.; Park, D.; Park, E.Y. Study on the Indoor Air Quality of Seoul Metropolitan Subway during the Rush Hour. Indoor Built Environ. 2008, 17, 361–369.
  29. Chatzidiakou, L.; Mumovic, D.; Summerfield, A.J. What do we know about indoor air quality in school classrooms? A critical review of the literature. Intell. Build. Int. 2012, 4, 228–259.
  30. Li, Y.; Leung, G.M.; Tang, J.; Yang, X.; Chao, C.; Lin, J.Z.; Lu, J.; Nielsen, P.V.; Niu, J.; Qian, H. Role of ventilation in airborne transmission of infectious agents in the built environment-a multidisciplinary systematic review. Indoor Air 2007, 17, 2–18.
  31. Wolkoff, P. Indoor air humidity, air quality, and health—An overview. Int. J. Hyg. Environ. Health 2018, 221, 376–390.
  32. Bräuner, E.V.; Frederiksen, M.; Kolarik, B.; Gunnarsen, L. Typical benign indoor aerosol concentrations in public spaces and designing biosensors for pathogen detection: A review. Build. Environ. 2014, 82, 190–202.
  33. Cepeda, M.; Schoufour, J.; Freak-Poli, R.; Koolhaas, C.M.; Dhana, K.; Bramer, W.M.; Franco, O.H. Levels of ambient air pollution according to mode of transport: A systematic review. Lancet Public Health 2017, 2, e23–e34.
  34. Han, X.; Naeher, L.P. A review of traffic-related air pollution exposure assessment studies in the developing world. Environ. Int. 2006, 32, 106–120.
  35. Prashant, K.; Patton, A.P.; Durant, J.L.; Christopher, F.H. A review of factors impacting exposure to PM 2.5, ultrafine particles and black carbon in Asian transport microenvironments. Atmos. Environ. 2018, 187, 301–316.
  36. Karanasiou, A.; Viana, M.; Querol, X.; Moreno, T.; De Leeuw, F. Assessment of personal exposure to particulate air pollution during commuting in European cities—Recommendations and policy implications. Sci. Total Environ. 2014, 490, 785–797.
  37. Nazelle, A.D.; Bode, O.; Orjuela, J.P. Comparison of air pollution exposures in active vs. passive travel modes in European cities: A quantitative review. Environ. Int. 2017, 99, 151–160.
  38. Kaur, S.; Nieuwenhuijsen, M.J.; Colvile, R.N. Fine particulate matter and carbon monoxide exposure concentrations in urban street transport microenvironments. Atmos. Environ. 2007, 41, 4781–4810.
  39. Knibbs, L.D.; Cole-Hunter, T.; Morawska, L. A review of commuter exposure to ultrafine particles and its health effects. Atmos. Environ. 2011, 45, 2611–2622.
  40. Loxham, M.; Nieuwenhuijsen, M.J. Health effects of particulate matter air pollution in underground railway systems—A critical review of the evidence. Part. Fibre Toxicol. 2019, 16, 12.
  41. Nieuwenhuijsen, M.J.; Gomez-Perales, J.E.; Colvile, R.N. Levels of particulate air pollution, its elemental composition, determinants and health effects in metro systems. Atmos. Environ. 2007, 41, 7995–8006.
  42. Xu, B.; Hao, J. Air quality inside subway metro indoor environment worldwide: A review. Environ. Int. 2017, 107, 33–46.
  43. Conceiçao, S.T.; Pereira, M.L.; Tribess, A. A Review of Methods Applied to Study Airborne Biocontaminants inside Aircraft Cabins. Int. J. Aerosp. Eng. 2011, 2011, 824591.
  44. Mangili, A.; Gendreau, M. Transmission of infectious diseases during commercial air travel. Lancet 2005, 365, 989–996.
  45. Annie, B.; Sacha, S.O.A.; Beck, C.R.; Nguyen-Van-Tam, J.S. The roles of transportation and transportation hubs in the propagation of influenza and coronaviruses: A systematic review. J. Travel Med. 2016, 23, tav002.
  46. Wen, Y.; Leng, J.; Shen, X.; Han, G.; Yu, F. Environmental and Health Effects of Ventilation in Subway Stations: A Literature Review. Int. J. Environ. Res. Public Health 2020, 17, 1084.
  47. Nielsen, P.V.; Olmedo, I.; Adana, M.R.D.; Grzelecki, P.; Jensen, R.L. Airborne cross-infection risk between two people standing in surroundings with a vertical temperature gradient. Hvac&R Res. 2012, 18, 552–561.
  48. Gupta, J.K.; Lin, C.H.; Chen, Q. Risk assessment of airborne infectious diseases in aircraft cabins. Indoor Air 2012, 22, 388–395.
  49. Furuya, H. Risk of transmission of airborne infection during train commute based on mathematical model. Environ. Health Prev. Med. 2007, 12, 78–83.
  50. Pestre, V.; Morel, B.; Encrenaz, N.; Brunon, A.; Lucht, F.; Pozzetto, B.; Berthelot, P. Transmission by super-spreading event of pandemic A/H1N1 2009 influenza during road and train travel. Scand. J. Infect. Dis. 2012, 44, 225.
  51. Abbasi, S.; Jansson, A.; Sellgren, U.; Olofsson, U. Particle Emissions from Rail Traffic: A Literature Review. Crit. Rev. Environ. Ence Technol. 2013, 43, 2511–2544.
  52. Ragettli, M.S.; Corradi, E.; Braunfahrlander, C.; Schindler, C.; De Nazelle, A.; Jerrett, M.; Ducretstich, R.E.; Kunzli, N.; Phuleria, H.C. Commuter exposure to ultrafine particles in different urban locations, transportation modes and routes. Atmos. Environ. 2013, 77, 376–384.
  53. Zhao, L.; Wang, J.; Gao, H.O.; Xie, Y.; Jiang, R.; Hu, Q.; Sun, Y. Evaluation of particulate matter concentration in Shanghai’s metro system and strategy for improvement. Transp. Res. Part D Transp. Environ. 2017, 53, 115–127.
  54. Park, J.H.; Woo, H.Y.; Park, J.C. Major factors affecting the aerosol particulate concentration in the underground stations. Indoor Built Environ. 2012, 23, 629–639.
  55. Jung, H.J.; Kim, B.; Ryu, J.; Maskey, S.; Kim, J.C.; Sohn, J.R.; Ro, C.U. Source identification of particulate matter collected at underground subway stations in Seoul, Korea using quantitative single-particle analysis. Atmos. Environ. 2010, 44, 2287–2293.
  56. Mendes, L.; Gini, M.I.; Biskos, G.; Colbeck, I.; Eleftheriadis, K. Airborne ultrafine particles in a naturally ventilated metro station: Dominant sources and mixing state determined by particle size distribution and volatility measurements. Environ. Pollut. 2018, 239, 82–94.
  57. Lee, Y.; Lee, Y.C.; Kim, T.; Choi, J.S.; Park, D. Sources and Characteristics of Particulate Matter in Subway Tunnels in Seoul, Korea. Int. J. Environ. Res. Public Health 2018, 15, 2534.
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