Airborne bioaerosols and their impact on human health.

Bioaerosols consist of aerosols originated biologically such as metabolites, toxins, or fragments of microorganisms that are present ubiquitously in the environment. International interests in bioaerosols have increased rapidly to broaden the pool of knowledge on their identification, quantification, distribution, and health impacts (e.g., infectious and respiratory diseases, allergies, and cancer). However, risk assessment of bioaerosols based on conventional culture methods has been hampered further by several factors such as: (1) the complexity of microorganisms or derivatives to be investigated; (2) the purpose, techniques, and locations of sampling; and (3) the lack of valid quantitative criteria (e.g., exposure standards and dose/effect relationships). Although exposure to some microbes is considered to be beneficial for health, more research is needed to properly assess their potential health hazards including inter-individual susceptibility, interactions with non-biological agents, and many proven/unproven health effects (e.g., atopy and atopic diseases).

Introduction

Bioaerosols are very small airborne particles (ranging from 0.001 to 100 μm) that originate biologically from plants/animals and can contain living organisms (Georgakopoulos et al., 2009). Therefore, pathogenic and/or non-pathogenic dead or alive microorganisms (e.g., viruses, bacteria, and fungi) may exist in bioaerosols (Mandal and Brandl, 2011). Bioaerosols are easily shifted from one environment to another because of their small size and light weight (Van Leuken et al., 2016). In recent years, exposure to bioaerosols in both occupational and residential environments has drawn much attention in light of their probable impacts on human health.

Sources of bioaerosol exposure in occupational activities are diverse enough to include waste sorting and composting, agricultural and food processing activities, the livestock industry, etc. (Pearson et al., 2015). Indeed, the prevalence of diverse respiratory diseases or symptoms (allergic asthma, rhinitis, airway inflammation, etc.) has been reported from workers susceptible to such exposure (Beck et al., 2012, Rohr et al., 2015). Bioaerosols were estimated to be responsible for approximately 5 to 34% of indoor particulate matter air pollution (Mandal and Brandl, 2011). The sources of indoor bioaerosol pollution include outdoor sources (passing through windows, doors, and ventilation); building materials; furnishings; occupants; pets; house plants; and organic wastes (Nazaroff, 2016). Regular or ordinary human activities (e.g., coughing, washing, toilet flushing, talking, walking, sneezing, and sweeping floors) are also capable of generating bioaerosols (Chen and Hildemann, 2009). However, basic environmental conditions, such as temperature and moisture content, can considerably influence the extent of their formation and dispersion due to their controlling effect on the formation of microorganisms (Dedesko et al., 2015). Consequently, the prevalence of bioaerosols can be associated with certain human diseases, such as pneumonia, influenza, measles, asthma, allergies, and gastrointestinal illness (Srikanth et al., 2008). However, under certain circumstances, exposure to some microbes is beneficial for health in terms of developing a healthy immune system and protect children from developing allergies and asthma (Severson et al., 2010). Although the importance of bioaerosols and their impact on human health has been recognized, it is yet difficult to accurately describe their role in the initiation or worsening of diverse symptoms and diseases. Table 1 presents the types of microorganisms and their resulting diseases. In this review, we give a comprehensive overview on bioaerosols based on the most recent publications covering this subject, with major emphasis on their compositions, and health effects. As a result, we hope that this review work will help researchers extend and establish better knowledge in relevant fields.

Table 1

Microorganisms and some of the major resulting diseases.

Order	Species	Approximate size	Resulting disease	Infection/transmission
1	Legionella pneumophila	Length: 2 μm Width: 0.3–0.9 μm	Legionnaires' disease	Inhalation of a water aerosol containing the bacteria
2	Mycobacterium tuberculosis	Length: 2–4 μm Width: 0.2–0.5 um	Tuberculosis	Person to person through the air
3	Bordetella pertussis	Length:40–100 nmDiameter: 2 nm	Whooping cough	Direct contact or inhalation of airborne droplets
4	Yersinia pestis	Length: 1–3 μmWidth:0.5–0.8 μm	Pneumonic plague	Being bitten by infected rodent flea or by handling infected animals
5	Bacillus anthracis spore	Length: 3–5 μmWidth: 1.0–1.2 μm	Anthrax	Contact with infected animals, flies, and the breathing of air containing anthrax spores
6	Variola vera	Length: 220–450 nmWidth:140–260 nm	Smallpox	Inhalation of airborne variola virus, prolonged face-to-face contact with an infected person, direct contact with infected bodily fluids or contaminated objects
7	Herpesvirida, HHV-3	Diameter: 150–200 nm	Chickenpox and shingles	Direct contact with fluid from the rash blisters caused by shingles
8	Morbillivirus measles	Length: 125–250 nmDiameter: 21 nm)	Measles, mumps, and rubella	Bodily fluids: drops of saliva, mucus from the nose, coughing or sneezing, tears from the eyes, etc.
9	Varibrio Cholerae	Length: 1.4–2.6 μmWidth: 0.5–0.8 μm	Cholera	Bite of contaminated food or a sip of contaminated water
10	Salmonella Typhi	Length: 0.7–1.5 μmThickness: 28 μm	Typhoid	Through contaminated food or water and occasionally through direct contact with someone who is infected
11	Microsporum Trichophyton	Length:5–100 mm Width: 3–8 mm	Ringworm	Direct or indirect contact with skin or scalp lesions of infected people, animals or fomites

Sampling of bioaerosols

It is reasonable to expect that the presence of each type of bioaerosol should reflect unique environmental conditions facilitating its formation and the mechanical stresses. The selection of sampling tool for airborne bioaerosol should thus be more delicate than those commonly employed for the general analysis of particle composition. However, as the sampling methods are not yet well defined for such specific purposes, the methods developed for general purposes can be applied for the sampling of bioaerosol with or without modifications: (i) impingers, (ii) cyclones, (iii) impactors, (iv) filters, (v) spore traps, (vi) electrostatic precipitation, (vii) thermal precipitators, (viii) condensation traps, (ix) gravitational samplers (e.g. settle plates), etc. (Haig et al., 2016). Instrumental setups of some of these samplers are shown in Fig. 1 . Usually these sampling devices separate particles from the air stream for their stable collection in or on a preselected medium (Jensen and Schafer, 1998). Gravitational sampling is passive (non-volumetric) to facilitate the collection of particles by gravitional force on coated microscope slide, agar plates, etc. (Wang et al., 2001). For inertial bioaerosol samplers, a number of options are available to include impactors, sieves, and stacked sieves. These setups allow the collection of particles by size selective sampling as they rely on the properties of particle to deviate from airflow streamlines due to inertia (Haig et al., 2016). Non-inertial samplers (e.g., filtration, electrostatic precipitation, thermal precipitators, and condensation traps) do not rely on inertia of particles for operation; thus, they are less reliant on particle size (Ghosh et al., 2015).

Fig. 1

Instrumental setups for bioaerosol sampling.

Bioaerosol samples are usually collected into liquid media or on solid filters. As they do not dry out and keep their viability, the use of liquid media may cause less stress on the bioaerosol components (Lehtinen et al., 2013). Nonetheless, as such an application is still limited for analysis of the effects of size segregation, it is less preferable to conduct in-depth assessment of bioaerosols.

Airborne particles are collected into a liquid collection medium in impingers and/or cyclones method. Impingers are operated by channeling air flow through nozzles to the collection chamber containing liquid. Hence, a number of factors (e.g., the air flow rate and distance between nozzle outlet and the surface of the liquid) influence the size diameter of the particles to be collected (Han and Mainelis, 2012). In a cyclone sampler, air is forced into the collection chamber through a spiraling, swirling flow. To escalate the sampling efficiency, a film of liquid can be added through the inlet of the cyclone as a cyclone wall under wet conditions. The liquid can then be collected for analysis at the bottom of the cyclone (McFarland et al., 2010. The air flow reverses its direction upon reaching the base of the cyclone. Then, the uncollected particles are carried out of the cyclone via a vortex finder placed in the top of the cyclone (McFarland et al., 2010). The bioefficiency can also be reduced through evaporation or as particles adhere internally on the walls of the collection chamber (Hoisington et al., 2014). In a new cyclone sampling technique, the samples are collected in standard centrifuge tubes from the top of the sample chamber unlike a conventional cyclone (e.g., collection from side) (Macher et al., 2008). Such bioaerosol samples can be processed immediately in these tubes. Hence, there is no need to transfer samples from the collection vessel to a new tube, making the processing much easier and simpler (Macher et al., 2008). Cyclone samplers with the multiple tubes are also efficient enough for collecting size-fractionated samples: large bioaerosol (initial (centrifuge) tube), medium-sized particles (second tube), and the smallest ones (filter)) (Macher et al., 2008).

The use of impactors depends on the inertia of particles for the collection. Therefore, the air sample containing bioaerosols is forced to pass through a set of curve streamlines. In this technique, low inertia particles are transported by the streamlines to avoid capture, while those with high inertia cannot follow the 90° curve of the streamlines. They can impact the agar plate while being influenced by the centrifugal force (Xu et al., 2013). This feature makes an impactor sampler highly suitable to classify all different particles into diverse size fractions. Because particles with comparatively bigger size fall out of the air flow, while those of smaller particle size remain airborne (Xu et al., 2013).

The bioaerosol samples are eventually collected onto certain media, most commonly filters through which they can be transferred onto plates or dissolved into a liquid solution for further microscopic examination or culturing experiments (Wu et al., 2010). Fibrous filters are made of a mat of fine fibers arranged in such a way that particles are captured on the fibers when they pass through the filter. Furthermore, such filters have complex pore-like structure where the particles are deposited (Uhrbrand et al., 2011). However, the efficiency of the filter sampling should be affected by the combined effects of several variables like microbial species, type of membrane filter, relative humidity, and sampling time (Wang et al., 2001). For detecting airborne bioaerosols, one should rely on many forms of cultivation media such as malt extract agar (MEA) (Lehtinen et al., 2013), Sabouraud dextrose agar (SDA) (Park et al., 2011), dichloran rose-bengal chloramphenicol (DRBC) (Tolvanen and Hänninen, 2006), and yeast extract glucose chloramphenicol (YGC) (Borrego et al., 2012). In one of the previous studies, Thorne et al. (1992) concluded that the all-glass impinger method was the best method for collecting total bacteria and fungi while the microbial sampler method was used preferably for sampling enteric organisms. In another study, it was also found that impingers for sampling airborne bacterial bioaerosols could be used with a better performance than filtration methods (Li, 1999).

Components of bioaerosols

Bioaerosols contain microorganisms and their components such as fungi, bacteria, endotoxin, mycotoxins, and allergens. Such organisms are well known normal components of both indoor/outdoor air. The concentration levels of different bioaerosols in air samples in different locations are summarized in Table 2 . Detailed descriptions of a list of key bioaerosol components are given below.

Table 2

Comparison of the concentration levels of bioaerosols in air samples.

Site	Location	Bacteria (CFU/m3)	Fungi(CFU/m3)	Endotoxin(ng/m3)	1,3)-β-d-glucan(ng/m3)	Reference
Wastewater treatment plant	Middle East	1016 to 1973	Not done (ND)	ND	ND	Niazi et al. (2015)
Contemporary airtight dwellings	USA	19 to 607	3 to 59	ND	ND	McGill et al. (2015)
Large office buildings	California, USA	67 to 206	ND	ND	ND	Tsai and Macher (2005)
Plant canopies	USA	46 to 663	ND	ND	ND	Lindemann et al. (1982)
six hospital lobbies	South Korea	270 to 1800	11 to 220	ND	ND	Park et al. (2013)
Amphitheater	China	209 to 838	ND	ND	ND	Guan et al. (2015)
Inside residential houses	Ohio, USA	ND	ND	ND	0.81–1.2	Crawford et al. (2009)
Outside residential houses		ND	ND	ND	6.1–8.9
Commercial concentrated animal feeding operations	Illinois, USA	ND	ND	98 to 23,157	2.4 to 538	Yang et al. (2013)

Fungi and bacteria

Many species of common fungi grow on various foods or other organic materials (e.g., paper, textiles, wood, and damp). Hence, allergens, enzymatic proteins, toxins, and volatile organic compounds (VOCs) could be produced from fungi to cause diverse human health problems (e.g., toxic effects, irritations, infections, and allergies). Significant relationships have been found between meteorological parameters (especially, relative humidity) and bacterial and fungal growth (Niazi et al., 2015). The outdoor concentrations of fungal and bacterial bio-aerosols were found to increase during monsoons (Kang et al., 2015). The prime sites for growth of bacteria and fungi were determined to include dehumidifier drip pans, humidifier reservoirs, air conditioning equipment, toilets, shower heads, water damaged carpets, damp ceiling panels, and walls (McGill et al., 2015). For example, relationship between the concentrations of bacterial bioaerosols and the number of users in public restrooms is shown in Fig. 2 .

Fig. 2

Concentration of bacterial bioaerosols in public restrooms and the number of users (Lee et al., 2012).

The results of previous studies confirm the considerable effects of seasonal factors on the observed levels of bioaerosols. In a wastewater treatment unit in Tehran, Iran, the average concentrations of bacterial bioaerosols in winter and summer were measured as 1016 and 1973 colony-forming unit (CFU)FND/m3, respectively (Thorne et al., 1992). The concentrations of fungi and bacteria measured from the bedroom of six contemporary, airtight dwellings in the USA during winter ranged from 3 to 59 (mean 18.4) and 19–607 (mean 212) CFU/m3, respectively (McGill et al., 2015). The findings of relatively low concentration levels from those samples also suggest that the filtration of air through the mechanical ventilation heat recovery (MVHR) system should have limited the migration of outdoor fungi and bacteria. Bacterial bioaerosol concentrations were generally low (from 0 to 118 (mean 11) CFU/m3) in the winter. Such result was found as the bacteria have adapted at the typical body temperatures of 30–40°C (Smirnova et al., 2001). In the Seoul Metropolitan area, S. Korea, the fungal bioaerosols were in the range of 24 to 654 (mean 177) CFU/m3 during winter (Lee et al., 2016). In contrast, their values in summer increased moderately to vary from 60 to 930 (mean 357) CFU/m3 (Heo et al., 2014).

In Malaysia, the average concentrations of bacteria in indoor and outdoor air were found as 1025 ± 612 and 1473 ± 1261 CFU/m3, respectively, while their fungal bioaerosol counterparts were 292 ± 83 and 401 ± 235 CFU/m3 (Hussin et al., 2011). These authors observed that the mean concentrations of bacteria and fungi in laboratories were as high as 320 and 460 CFU/m3, respectively, while their lowest counterparts in office rooms were 61 and 140 CFU/m3. Likewise, the concentrations of bacteria measured in areas without occupants were considerably lower than those with occupants (p  < 0.05) (Adams et al., 2015). As such, the number of occupants and their activity were likely to sensitively affect the concentration levels (and compositions) of indoor bacteria. Moreover, insufficient ventilation was also suggested to exert control on the levels of viable bacteria in indoor air (Yoon et al., 2011).

Endotoxins

Endotoxins are characterized as lipopolysaccharides (LPS) in Gram-negative bacteria with very high pro-inflammatory properties (Armstrong et al., 2013). Endotoxins consist of such components as: (1) a core polysaccharide chain, (2) O-specific polysaccharide side chains (O-antigen), and (3) a lipid component, Lipid A, responsible for the toxic effects (Tirsoaga et al., 2007). Human exposure to endotoxins occurs constantly, as they can easily bind to dust (i.e., easily inhalable) (Wallace et al., 2016). Response to endotoxins varies due to such factors as dose, location, and route. Exposure to endotoxins was suggested to a cause decrease in lung diffusion capacity along with diverse symptoms and diseases, such as fever, shivering, blood leukocytosis, neutrophilic airway inflammation, arthralgia, dyspnea and chest tightness, and bronchial obstruction (Thilsing et al., 2015).

Endotoxins have been considered to be one of the main factors contributing to occupational lung diseases and organic dust toxic syndrome (Park et al., 2015). In fact, changes in pulmonary function due to endotoxin exposure have been reported from several occupational groups: textile workers (geometric mean (GM): 2160 EU/m3 (Paudyal et al., 2011), dairy workers (GM: 329 EU/m3 (Mitchell et al., 2015), animal feed and grain workers (GM: 662 EU/m3), and sewage treatment plant workers (GM: 214 EU/m3) (Cyprowski et al., 2015).

β glucans

β glucans are glucose polymers that occur naturally in the cell walls of various microorganisms (e.g., bacteria, algae, lichens, fungi, yeasts, and plants (like oats and barley)) (Kurek et al., 2016). In a previous study conducted in Ohio, USA, GM concentrations of β glucans in indoors and outdoors were measured as 1.0 (range: 0.81–1.2) and 7.34 ng/m3 (range 6.1–8.9), respectively (Crawford et al., 2009). Airborne concentrations of (1,3)-β-d-glucan, measured from six sites (office, hospital, student dormitory, subway station, and a commercial street) in Beijing, China, were found to range from 0.02 to 1.2 ng/m3 (Dong and Yao, 2010). In another study conducted in 18 commercial concentrated animal feeding operations in Illinois, USA, the airborne concentration of (1,3)-β-d-glucan ranged from 2.4 to 538 ng/m3 (Yang et al., 2013). β glucans have been used to boost the immune system and also to treat high cholesterol, diabetes, and cancer (Holst et al., 2015). However, many studies have reported that exposure to airborne β glucans might induce inflammatory responses and associated respiratory symptoms (Richter et al., 2015). Hence, the effects of β-glucans inhalation appear to vary in relation to such variable (e.g., the type of glucan and concomitant exposure).

Mycotoxins

Mycotoxins are toxic secondary biomolecules produced by fungus or molds. However, different types of mycotoxins may be produced by one mold species, while the same mycotoxin may be produced by several species (Andretta et al., 2011). Hence, classification of mycotoxins can be made based on their chemical structures as well as reactive functional groups (e.g., primary/secondary amines, carboxylic acids, hydroxyl (or phenolic) groups, lactams, and amides) (Grenier and Applegate, 2013). The health effects of mycotoxins on humans and animals are diverse enough to include weakened immune systems, allergies or irritations, many identifiable diseases, and even death. The effects of mycotoxicosis should depend on the type of mycotoxins, the duration of exposure, concentration levels, and the conditions of the exposed individual (e.g., age, health, and sex) (Marin et al., 2013). Moreover, the severity of such poisoning, if taking place, can be compounded by many variables (e.g., alcohol abuse, vitamin deficiency, caloric deprivation, and infectious disease status) (Marin et al., 2013). Exposure to mycotoxins occurs most often via ingestion, inhalation of spore-borne toxins, as and dermal contact on mold-infested substrates.

Allergens

An allergen is any substance (antigen), most often eaten or inhaled, that causes an unusual immune response and triggers an allergic reaction. The most common symptoms of allergens (e.g., runny nose, stuffy nose, scratchy throat, itchy eyes, and sneezing). However, the risk of asthma and other allergic diseases can increase, if exposed to allergen to a certain degree (Baxi and Phipatanakul, 2010). Allergens can be found in a variety of sources, such as fungi (spores and hyphae), arthropods (mites and cockroaches), vascular plants (fern spores, pollen, and soy dust), pet dander, and royal jelly (Jutel et al., 2016). Many factors (e.g., mechanical disturbance, wind, rain, or active discharge mechanisms) exert the control on the release of particles into the air. Indoor humidity and water damaged items (e.g., carpets, ceilings, and walls) are important sources of mite and mold allergens (Peden and Reed, 2010).

Potential health effects of bioaerosols

In most situations, the formation of bioaerosols occurs in the form of complex mixtures of allergens, toxins, and other miscellaneous ones. Exposure to bioaerosols tends to be associated with various health effects (e.g., infectious diseases, acute toxic effects, allergies, and cancer). However, as respiratory symptoms and impairment of lung function have been the most widely studied subjects, they probably belong to the most important health problems caused by bioaerosols.

Infectious diseases

Infectious diseases arise from exposure to biological agents (e.g., bacteria, viruses, fungi, and parasites) through the transmission of infectious agents by direct (i.e., licking, touching, biting) and/or indirect contact (i.e., cough or sneeze), airborne transmission, and vector-borne transmission (Chretien et al., 2015). Zoonotic infections (e.g., Q-fever, brucellosis, anthrax, and avian and swine influenza) are predominantly attributed to livestock farms, veterinary practices, abattoir, and animal store workers (Wu et al., 2015). Among 44 seroepidemiological studies, 37 (84%) were identified to be subject to an enhanced risk of zoonotic pathogen infection (Baker and Gray, 2009). Infected veterinarians may act as biological sentinels to spread zoonotic pathogens to the surroundings (e.g., community members, their families, and the animals they care). For instance, the Chlamydophila psittaci bacteria are highly prevalent in psittacine birds and pigeons (Vanrompay et al., 2007, Ling et al., 2015). People are mostly infected through inhalation and/or being exposed to petting infected birds, C. psittaci-infected aerosols, and handling infected avian tissues (West, 2011). In the Netherlands, a three-year (2007–2009) cumulative epidemic of Q fever took place due to the airway transmission of the causative micro-organism Coxiella burnetii via infected dairy goat farms (Commandeur et al., 2014). Due to this outbreak, more than 4000 patients were reported to visit Municipal Health Services (MHS) over that period (Roest et al., 2011). The epidemic ended through taking the control measures on dairy goat and sheep such as hygiene measures, vaccinations, and the culling of pregnant infected animals (Dijkstra et al., 2012).

In a human dose–response model, Brooke et al. (2013) found that the dose required for 50% of the exposed population to become infected (infd50) was 1.5 bacteria (95% confidence interval (CI): 0.75–38.7), indicating high infectivity of Coxiella burnetii via aerosol exposure. In Italy in 2013, three poultry workers were diagnosed with conjunctivitis during an outbreak of influenza A (H7N7) virus among poultry (Puzelli et al., 2014). Bioaerosols are also associated with Legionnaires' disease as long as many different forms of bacterial pneumonia, influenza, measles, coccidioidomycosis, and gastrointestinal illness. People are exposed to Legionella when they breathe in a mist or vapor containing the associated bacteria (Berrington and Hawn, 2013). The severity of such infection can vary broadly from mild febrile illness (Pontiac fever) to a potentially fatal pneumonia (Berrington and Hawn, 2013).

When a person inhales Mycobacterium tuberculosis (Mtb)-contaminated air, the inhaled bacteria are likely to reach the lungs and cause tuberculosis (TB) (Pedersen et al., 2016). The lungs or larynx of the TB patients then were found to release the bacteria to the surroundings, as they cough, sneeze, talk, and expel air or disperse droplets that contain M. tuberculosis (Pedersen et al., 2016).

The occurrence of TB poses a significant risk of transmission in healthcare and other congregate settings (e.g., prisons, jails, and homeless and social assistance shelters). A meta-analysis study reported that the average annual risk of developing TB for healthcare workers (across all settings) was three times higher (95% CI 2.43–3.51) than that of the general population (Baussano et al., 2011). Bordetella pertussis, known as the agent of whooping cough (pertussis), is transmitted primarily via droplets (Solano et al., 2014). As a result of the infection, colonization and rapid multiplication of the bacteria may occur on the mucous membranes of the respiratory tract. The potential sources of infant (under 6 months old) pertussis infections from nine studies were identified as mothers, fathers, and grandparents in 39% (95% CI 33–45%), 16% (95%CI 12%–21%), and 5% (95% CI 2%–10%) of cases, respectively (Wiley et al., 2013). Furthermore, teachers, health care workers, and children could be easily exposed to or transmitting the disease to others (Rohani and Drake, 2011).

Pneumonic plague is another deadly infectious and transmittable disease when fine infective droplets are inhaled (Hammamieh et al., 2016). A total of 21,725 cases of human plague were reported globally during 2000 to 2009 including 1612 deaths (Butler, 2013). As an infectious disease caused by the bacterium (Bacillus anthracis), Anthrax is spread through the intestines (ingestion), lungs (inhalation), or skin (cutaneous) (Berger et al., 2014, Azarkar and Bidaki, 2016). Exposure to infected animals (or their skin, wool, and meat) is the usual pathway of anthrax to humans (Navdarashvili et al., 2015).

Measles is another acute viral disease which can be accompanied by pneumonia, blindness, brain damage, and even death (Zachariah and Stockwell, 2016). In 2013, more than 20 million infections of measles occurred worldwide causing around 145,000 deaths (CDC, 2015). Measles is caused by rubeola virus, a paramyxovirus of the genus Morbillivirus. It is known to be spread through droplet transmission from the nose, throat, and mouth of the infected persons if they cough or sneeze (Clemmons et al., 2015). The infected droplets that land on the surface may remain active to be contagious for few hours. People may contact the virus by rubbing their eyes or by putting virus-infected fingers in their nose or mouth. Among unimmunized people exposed to the virus, over 90% will have the disease (Phadke et al., 2016).

Over 200 different viral types are responsible for common cold. Among them the most commonly implicated viruses are rhinovirus, human coronavirus, respiratory syncytial virus (RSV), and adenoviruses which have been identified to bring on about 30%–80%, 15%, 10%–15%, and 5% of colds, respectively (Allan and Arroll, 2014). These viruses can spread as airborne droplets (aerosols) or through many other routes (e.g., direct contact with contaminated objects (e.g., utensils, towels, keyboards, toys, and telephones) or with infectious (nasal) secretions (Arroll, 2011).

Streptococcus pneumoniae bacteria can cause several different types of infection through lungs, ears, nose, bacteremia (blood stream), and meningitis (spinal cord and brain) (Daniels et al., 2016). It was reported that Streptococcus pneumoniae should most commonly inflict children, the elderly, and other people with weakened immune systems (Hamborsky et al., 2015). According to the World Health Organization (WHO), Streptococcus pneumoniae killed around half a million children (under 5 years old) worldwide every year (Knoll et al., 2009). Streptococcus pneumoniae bacteria usually spread through the air in the form of aerosol droplets through coughing and sneezing and also through contact with an infected person (Richter et al., 2013).

Respiratory diseases

The human lung is subjected to airborne pollutants and irritants with each breath. Generally, respiratory symptoms result from the inflammation of airway when exposed specifically to allergens, toxins, or pro-inflammatory agents. According to the community based follow-up of 422 Canadian children, beta-glucan exposure at age 7–10 years was found to develop and persist atopic/non-atopic asthma (Odd Ratio (OR = 1.79, 95% CI: 1.14–2.81) while bronchial hyper-responsiveness (BHR) (OR = 1.74, 95% CI: 1.05–2.89) at ages 11–14 (Maheswaran et al., 2014). Lin et al. (2012) reported that asthma cases had higher odds of being sensitized to Derp dust mites (OR = 1.94, 95% CI: 1.13–3.35), cat (OR = 1.96, 95% CI: 1.13–3.39), or dog allergens (OR = 1.89, 95% CI: 1.10–3.22) than the controls. Nevertheless, mold sensitivity is positively related with asthma intensity (Ma et al., 2015). Associations with asthma were found with mold in children's bedrooms (OR = 4.82, 95% CI: 1.29–18.02) and in living rooms (OR = 7.51 95% CI: 1.49–37.8) (Karvonen et al., 2015).

Asthma and pollen exposure have been found to have decreased lung activity while increasing pulmonary inflammation (Baldacci et al., 2015). The simultaneous presence of sferics and grass pollen escalate the risk of an asthma epidemic by 15% (Canova et al., 2013). Endotoxins and glucans from bacteria and molds, in addition to irritating airways, were also suggested to contribute to airway inflammation (Hoppin et al., 2014). A decrease in lung function was found to occur by inhalation of over 80 mg of endotoxins in healthy subjects and over 20 mg of endotoxins in asthmatics (Kharitonov and Sjöbring, 2007).

Cancer

The possible associations between exposure to bioaerosols and some specific cancers have been reported (Hayleeyesus et al., 2015). Johnson and Choi (2012) reviewed lung cancer risk of workers in the meat/poultry industry. They concluded that even after controlling for smoking there was about 30% excess risk of lung cancer among them. Furthermore, meat and poultry plant workers were suspected to be exposed to high concentrations of airborne mixture including fecal material, dander (skin material), feather, and micro-organisms (e.g., virus, endotoxins, fungi, and bacteria). The dose–response relation, when assessed by lung cancer among meat workers, indicated the potent role of the exposure to biological materials in the form of animal urine, feces, and blood (possibly oncogenic zoonotic viruses) (McLean et al., 2004). From a pilot case-cohort study (30,411 poultry workers under the high risk of exposure vs. 16,408 control subjects), pancreatic/liver cancers were found to be caused from the slaughtering of poultry (OR = 8.9, 95% CI: 2.7–29.3)/OR = 9.1, 95% CI: 1.9–42.9); the catching of live chickens (OR = 3.6, 95% CI: 1.2–10.9)/OR = 1.0, 95% CI: 0.1–8.5); and the killing of other types of animals for food (OR = 4.8, 95% CI: 1.5–16.6)/OR = 2.0, 95% CI: 0.2–18.2) (Felini et al., 2011). These authors also recorded pancreatic cancer cases among workers who have ever worked on a pig farm as OR = 3.0, 95% CI: 1.0–8.2.

In another study, elevated risk for poultry oncogenic viruses was recorded who (1) killed chickens (OR 4.2, 95% CI 1.2 to 14.7; HR 1.8, 95% CI 1.0 to 3.3) and (2) had direct contact with chicken blood at work (OR 1.9, 95% CI 1.0 to 3.8; HR 1.3, 95% CI 0.9 to 2.0). Elevated risk of lung cancer due to poultry exposure was recorded for subjects who killed chickens at work (OR 4.2, 95% CI: 1.2–14.7) and ever had direct contact with chicken blood at work (OR 1.9, 95% CI: 1.0–3.8) (Felini et al., 2012). Furthermore, studies have found that those who worked as chicken slaughterer have around nine times the odds of both pancreatic/liver cancer compared with those with no such exposure (ACS, 2016). In an exploratory study with a total of 46,819 workers in poultry/non-poultry plants, higher risk of brain cancer was related with killing chickens (OR = 5.8, 95% CI: 1.2–28.3) and working in a shell-fish farm (OR = 13.0, 95% CI: 1.9–84.2) (Gandhi et al., 2014).

Guidelines and assessment of exposure risk to bioaerosols

Because of limited data and enormous variability in the potential health effects between different types of bioaerosols, standards for bioaerosols based on health risk assessments are still impractical (Lee et al., 2012). The Environment Protection Agency (EPA) of the US and the World Health Organization (WHO) do not have any specific guidelines for bioaerosol concentration levels (WHO, 2009). In contrast, the Occupational Safety and Health Administration (OSHA) has set a standard guide for nonspecific dusts as total dust (15 mg/m3) and respirable dust (5 mg/m3) (OSHA, 1992). The Health and Welfare Department in Canada also established the following guidelines: (i) 50 CFU/m3 for one species of fungi warrants immediate investigation; (ii) 100 CFU-m− 3 is unacceptable for the presence of certain fungal pathogens; (iii) 150 CFU/m3 of mixed species is normal; and (iv) up to 500 CFU/m3 should be acceptable if dominated by Cladosporium (WHO (World Health Organization), 1988, EC (Environment Canada), 1989). In the case of Korea, the maximum allowable concentration of total bacterial bioaerosol is 800 CFU/m3 (Ministry of Environment, Republic of Korea, 2010).

Table 3 summarizes the standards/guidelines for bioaerosols proposed by different governmental and private organizations. Based on European literature databases on residential indoor air quality, the residential limit values for airborne fungi, bacteria, and bacterial endotoxin were proposed as 5 × 103  CFU/m3, 5 × 103  CFU/m− 3, and 5 ng/m3, respectively (Górny and Dutkiewicz, 2002). These guidelines are generally based on baseline bioaerosol concentrations, without taking into account of effects on human health. The proposed threshold bioaerosol concentrations were generally taken from the data associated with culturing assays. Furthermore, various international round robin tests indicated correlations between laboratories results but considerable differences in absolute levels.

Table 3

Summary of quantitative standards and guidelines for bioaerosols in air by governmental and private organizations.

Organization	Guideline	Remarks	Reference
American Conference of Governmental Industrial Hygienists (ACGIH)	• < 100 CFU/m3	Low	Macher et al. (1995)
	• 100–1000 CFU/m3	Intermediate
	• > 1000 CFU/m3	High
American Industrial Hygiene Association (AIHA)	There is no safe level of an uncontained pathogenic organism		AIHA (1986)
Commission of the European Communities (CEC)	For houses		CEC (1994)
	• < 50 CFU/m3	Very low
	• < 200 CFU/m3	Low
	• < 103 CFU/m3	Intermediate
	• < 104 CFU/m3	High
	• > 104 CFU/m3	Very high
Healthy Buildings International	< 750 CFU/m3	Total airborne bacteria and fungi is OK if species are not infective or allergenic	Rao et al. (1996)
Indoor Air Quality Association (IAQ)	• < 300 CFU/m3	Common fungi is OK	IAQA (1995)
	• < 150 CFU/m3	Mixed fungi other than pathogenic orexigenic is OK
IAQ in office buildings: a technical guide	• > 50 CFU/m3	One species should be investigated	Malmberg (1991)
	• < 150 C CFU/m3	If mixture of species is OK
The Netherlands/research methods in biological indoor air pollution	• > 104 CFU/m3	Total fungi is a threat to health	Heida et al. (1995)
	• > 500 CFU/m3	One species of potentially pathogenic nature is a threat to health
Occupational Safety and Health Administration (OSHAA)	• > 1000 CFU/m3	Indicates contamination	OSHA (1994)
	• > 106 fungi/g of dust	Indicates contamination
Environment Canada (EC)	•Pathogenic and toxigenic fungi	Unacceptable in indoor air	EC (1989)
	• > 50 CFU/m3	One species should be investigated
	• < 150 CFU/m3	OK if mixture of species
	• < 500 CFU/m3	OK if Cladosporium or other common phylloplane
Ministry of environment (ME), Republic of Korea	< 800 CFU/m3	OK	Ministry of Environment, Republic of Korea (2010)

At present, a wide variety of options are available for sampling instrumentation and analytical methods although no standard method has been established for enumerating bioaerosol. However, the apparent concentrations of airborne bioaerosol are greatly dependent on the environmental conditions (e.g., temperature, relative humidity, and airflow) along with the variables associated with analytic approaches employed by the investigator. It is also necessary to accurately analyze all microbial cells suspended in the air and to differentiate those which are metabolically active, culturable, and non-viable.

Existing quantitative standards and guidelines tend to suffer from lack of evidence in human dose/response relationship, reliance on short-term grab samples (culture-based analysis), and the absence of standardized protocols (in all of the procedures of data collection, analysis, and interpretation). Exposure guidelines thus should not be established until a standard methodology is available. Without scientifically proven standards and guidelines, arbitrary criteria may lead to inappropriate testing and test interpretations (WHO, 2009). Moreover, the consequences of misleading sampling data can be significant in terms of litigation, labor grievances, disability claims, inappropriate medical treatment, or recommendation to demolish public buildings. Therefore, further validation and standardization are needed for establishing procedures for quantification of bioaerosol (e.g., sampling, extraction, and analytical procedures) (Ghosh et al., 2015).

Furthermore, there are a few latest technologies (e.g., polymerase chain reaction (PCR), Enzyme-linked immunosorbent assay (ELISA), and Metagenomics) are currently used for microbial analysis. PCR is a technique used in microbial community analysis for synthesizing multiple copies (amplifying) of a specific piece of deoxyribonucleic acid (DNA). This technique is very rapid (results usually available within 12 to 26 hr), high degree of sensitivity (able to detect one colony forming unit in a 25 g sample), precise and accurate, flexible (assays for more than one pathogen can be run simultaneously) (DeAngelis et al., 2011). ELISA is also an analytical technique that uses components of the immune system (such as IgG or IgM antibodies) and chemicals to detect the presence of an antigen or antibody in a given sample (Verma et al., 2013). The variations in ELISA allow us to detect either antigen or antibody, identifying the different strains of microbes at a time, and also in characterization of the epitope distribution on the microbial surface (Verma et al., 2013).It shows wider applications in clinical diagnosis, in pathological studies, and in quality control studies. Metagenomics applies direct genetic analysis tools to access the genetic content of entire communities of organisms (Cha et al., 2017). Metagenomics gives genetic information on potentially novel biocatalysts or enzymes, genomic linkages between function and phylogeny for uncultured organisms, and evolutionary profiles of community function and structure (Thomas et al., 2012). The metagenomics approach can also serve as a powerful tool for elucidating the relationship between host-associated microbial communities and host phenotype (Banerjee et al., 2015).

Conclusions

The presence of bioaerosols has been suspected as the cause of various human diseases covering not only infectious/respiratory symptoms but also cancer. Bioaerosols are also found in most enclosed environments owing to their ubiquitous presence in nature. Even higher bioaerosol concentrations may be observed in indoors (compared to outdoors) due to various internal sources that are generally associated with human activities. Hence, increasing the mechanical or natural ventilation rate and regular cleaning and maintenance activities can play a vital role in increasing indoor air quality. However, even under ideal conditions for preventative maintenance, chances of exposure to bioaerosols persist. In light of the fact that many uncertainties still remain in exposure assessment (i.e., poorly developed tools for quantitation of risks), efforts to resolve such issues should be developed in many respects. There are various types and non-ideal microbiological techniques available for sampling and analysis of bioaerosols (and the extent of their exposures) that have left much confusion and many misconceptions. Until new and reliable techniques are introduced, a common protocol for their quantitation based on currently available methods is to be employed to offer a near-uniform basis to allow cross-comparison between different experimental data sets. Therefore, more research is desirable to properly establish better assessment tools for the exposure to bioaerosols and its validation.