Air pollution can harm nearly every organ in the body1,2, and particulate matter (PM) is the main offender. PM has been classified by particle size, which is an important factor in its health effects. PM10 (particles ≤10 µm in diameter), PM2.5 (particles ≤2.5 µm in diameter), also called fine particles, and PM0.1 (particles ≤0.1 µm in diameter), also called ultrafine particles (this term is used interchangeably with PM0.1 in this document), have different health effects that, in part, result from how these particles navigate the small bronchioles and lung defenses. PM0.1 are also called nanoparticles because of their size, although many authors restrict the word “nanoparticles” to the 100-nm or smaller particles produced by controlled engineering processes3.

Ultrafine particles are dispersed atmospherically in many settings4. Examples are found in nature, from forest fires, ocean splashes, and viruses; combustion processes, from vehicular and power plant emissions and tobacco smoking; and synthetic sources, from toner pigment and many engineered products used for microtechnology. These particles may be formed by the coalescence of ions and gaseous molecules produced by combustion, often as acidic and basic ions or other charged species that combine to form more stable molecules or salts. This process, which usually depends on aqueous oxidation, may explain the sulfate levels of London fog of 19525 and the effects of humidity on the symptoms of patients with respiratory disease. Coalescing PM0.1 are a major source of PM2.5.

The harmful effects of the different PM categories overlap because the corresponding sizes overlap; PM10, which include all smaller particles, will have similar effects to those of smaller PMs, although the effects can be distinguished by taking mass into account. PM10 and PM2.5 are measured by their mass, while PM0.1 are measured by particle number.

Numbers of particles

A typical concentration of PM0.1 in ambient air in rural areas is 2610 particles/cm3, whereas a roadside concentration may be 48,180/cm3, with a mean global concentration of 10,760/cm34. The large numbers of PM0.1 quickly diminish by amalgamation into larger particles and atmospheric dispersion, resulting in local concentrations or “hotspots” near traffic or sites of industrial production. It is paradoxical that PM0.1 particle numbers decrease quickly by coalescence, yet remain airborne for extended periods and can travel to other continents. Peak concentrations of traffic emissions occur near curbsides, and these levels are often more than ten-fold higher than the background. The concentrations regress to background by ~500 m from the source6. High concentrations are associated with many different conditions, such as high humidity, low air movement, increased number of diesel vehicles, seasons, and traffic acceleration after stopping3. Improvements in fuel and engine technology and the use of catalytic converters have reduced the PM mass and carbon monoxide (CO) from automotive exhaust but have increased the number and toxicity of PM0.17,8.

Occupational exposures, especially those associated with combustion or high temperature, such as welding or blast furnace operation, may be great. The highest concentrations of PM0.1 are found in welding facilities, machine shops, basic metal industries, traffic-related occupations, and restaurants, with concentrations of 0.7–4.7 × 106, 60–450 times higher than the background levels3.

As particle sizes decrease, the numbers increase, especially when such particles approach the size of PM0.1. Coarse particles (PM10-2.5) accounted for <0.1% of the total particle numbers in a study from Shenyang, China9. An airborne concentration of 10 µg/m3 would require 2.4 × 106 20-nm particles, but only one 2.5-µm particle/cm3,10. With the particle number and total surface area as important parameters, the mass measurements used for PM10 and PM2.5 are not useful for PM0.1. Particle numbers are so much greater for PM0.1 that this measurement is used to estimate PM0.1 concentrations.

The variation in PM0.1 number with season and location was highlighted by a European study that found that Augsburg, Helsinki, and Stockholm had mean annual concentrations of particles between 10,000 and 11,000 cm−3, but winter concentrations were almost twice that much (between 10,000 and 20,000 cm−3), and summer concentrations were approximately half that much (between 5000 and 6000 particles cm−3. Rome and Barcelona, which have greater air pollution, had average annual concentrations of PM0.1 of more than 43,000 and 39,000 cm−3, respectively, but winter concentrations of 100,000 cm−3. This study also reported diurnal and week-day variations, with daily peak levels between 7 a.m. and 10 a.m. in most places. Sunday had ~2/3 of the weekday concentrations11. The variation and fluctuating nature of the exposure makes monitoring, gauging their health effects, and setting standards difficult.

The hourly average exposure over a year of PM0.1 differs from that of PM2.5 in that the distribution of PM0.1 is more skewed and widely spread owing to their more rapid reduction and dispersal. The greater diurnal trend for PM0.1 results from the variation in vehicular emissions. PM0.1 and PM2.5 are not well correlated; the ratio of the particle number-to-mass ratio was found to be highest at roadside sites (indicating a prominence of PM0.1) and lowest in polluted cities (indicating a prominence of PM2.5). Regulating PM2.5 may not significantly reduce PM0.112.

Absorption and retention of PM0.1

Most inhaled particles of 10 µm or larger in aerodynamic diameter impact the nasopharyngeal membranes. Inhaled particles of 5–10 µm usually land on the airways and are normally removed by alveolar macrophages and lung lymphatics1. Particles in the range of 1–2.5 µm usually make their way to the terminal bronchiole, the site of greatest accumulation and tissue destruction, as commonly seen in centrilobular emphysema. Particles <1 µm stay airborne longer and easily gain access to alveoli. Although most PM sizes can be engulfed by cells, PM0.1 translocate transcellularly across alveolar epithelial cells by diffusion through the lipid bilayer of the cell walls13. It is not just phagocytic cells that pick up material. All cells absorb cellular fragments of senescent, damaged, or normal cells and exchange and recycle molecular material14. The cellular fragments (sometimes termed extracellular vesicles) could easily harbor PM0.1.

In an in vitro model, investigators showed that positively charged PM0.1 penetrated cells 20–40 times more than negatively charged particles13. Although this result may be specific to the cells tested, it points out the importance of surface charge. An important property of PM0.1 is the large surface-area to mass ratio that allows the particles to carry large amounts of adsorbed materials per unit mass. The large variety of compounds that attach to these particles is likely to be a major cause of their toxicity, but the great variation of adsorbed material makes it more difficult to link PM0.1 to specific conditions. Other properties, such as aspect ratio, charge, surface reactivity, solubility, hydrophobicity or polarity, agglomeration state, and the ability to interact with biologic tissue and generate reactive oxygen species, are important determinants of toxicity.

PM0.1 that enter alveoli can be retained in surfactant15, thus sidestepping the mucociliary escalator clearance mechanisms. The retention half-life of titanium dioxide (TiO2) particles of the identical crystalline structure, deposition burden, and conditions in animal lungs was reported to be 170 days for 250-nm particles and 500 days for 20-nm particles16. The finer particles caused stronger and more persistent inflammation, with more type II cell proliferation and macrophage impairment and early interstitial fibrotic foci. The small particles also moved into the lung interstitium and periphery more than the larger ones16. TiO2, which is considered a safe additive to foods, toothpaste, lotions, and many other household products, appears to have many major toxic effects when its particles are in the PM0.1 range17.

Health effects

The first interaction site for PM0.1 is the lung. The surface area of the lung has been estimated to be more than 100 m2 18, but this is commonly estimated by measuring linear intercepts with a 1-µm probe by light microscopy. The estimate of the surface area becomes larger as the sampling probe becomes smaller, accounting for the additional surface area of an irregular surface. The surface area of the lung to a nanoprobe of PM0.1 would be orders of magnitude greater than the light microscopy estimates, something Weibel referred to as the “Coast of Wales” effect19.

PM0.1, along with their toxic baggage, easily reach the large surface of the lung. They subsequently gain access to other organs through the lung vasculature, either through mobile cells or freely in the vasculature and lymph to directly harm distal organs. Another mechanism by which PM0.1 cause harm is lung inflammation and the subsequent spread of inflammatory mediators to distal organs. This is considered the main cause of systemic toxicity for larger PM, which are less able to directly access other organs. In addition to having better access, PM0.1 have more toxicity in cellular and animal models20. For example, low-solubility and low-toxicity PM0.1 cause more inflammation in rat lungs than PM2.5 of the same material21.

Other explanations for the increased toxicity of PM0.1 include the fact that many smaller particles may stress alveolar macrophages more than fewer large ones. This could also explain why clearance is dependent on particle size. Inflammation in response to noxious material on the surface of particles and interactions with the cell surfaces of host tissues would also be greater with ultrafine particles22. Another important point when considering human population studies is that PM2.5 have more immediate effects, while PM0.1 have more delayed effects and a greater influence on mortality23. Most epidemiologic studies of acute exposure to PM0.1 take into account a lag time between exposure and symptoms of 1–5 days to account for the delayed effect.

Compared to data on PM2.5 and PM10, there is a paucity of information on the long-term health effects of PM0.1. A major reason for this is the lack of international standards and national reporting. Although PM0.1 can be readily measured in the atmosphere, the measuring instruments are not standardized, which means methods and protocols vary24. Developing standards is difficult for populations because of the variable nature of personal exposures and the silent nature of the effects of air pollution, particularly PM0.1. Neither clinicians nor the public generally consider air pollution as a cause of a specific illness. Many exposures, such as to office printers, would go unnoticed by most workers.

The study of PM0.1 has been aided by engineered nanoparticles. Ultrafine particles can be manufactured with a high degree of accuracy with regard to their size, shape, and composition. The biological effects of these factors can then be studied more precisely. Engineered nanoparticles can be applied to cells and tissues and given as a challenge to animals and human volunteers. For example, high doses of fibrous and tubular nanostructures can result in fibrotic lung reactions and an increased risk of carcinogenesis25. Single-walled nanotubes can persist deep in the lung and induce inflammatory and fibrotic reactions26. Many other studies have shown various intracellular effects depending on the species studied and the nature of the nanoparticle25.


A review of all diseases associated with PM0.1 is beyond the scope of this paper, but the following discussion highlights major associations. Air pollution and its effects on different organ systems have recently been reviewed1,2.


The respiratory system is usually the first line of entry into the body for air pollution, but ingested PM0.1 pass through the gastrointestinal tract and can stimulate immune responses in animals and human colonic biopsies. In a Western diet, more than 1012 ultrafine particles are ingested daily by a single person27. Intact skin is generally considered protective. Short-term exposure to PM0.1 with a high content of polycyclic aromatic hydrocarbons increases 8-hydroxyl-2-deoxyguanosine, a byproduct of DNA oxidative damage, in children with eczema but not in those without eczema28, although particles of zinc and TiO used in topical skin care have been shown to penetrate intact skin, especially in watery or oily vehicles29.

Metal fume fever and polymer fume fever

Metal fume fever is an example of a disease most likely caused by PM0.1. PM0.1 are produced by welding. Inhaling the small particles generates a great amount of reactive oxygen species, leading to inflammation30. Metal fume fever usually presents with malaise, fever, chills, arthralgias, and myalgias 4–8 h after exposure to metal fumes, usually through welding. Chest radiographs are inconsistent, and the syndrome generally abates without treatment. Although zinc oxide (ZnO) has been incriminated, other metals, namely, copper, magnesium, and cadmium, have also been identified. A similar syndrome, polymer fume fever, has been associated with inhalation of fluorinated polymer products, such as polytetrafluoroethylene (Teflon®). Heated polytetrafluoroethylene contains ultrafine particles (median diameter 26 nm) that are toxic to rats, causing hemorrhagic pulmonary inflammation and death with high-dose exposure and decreased function with low-dose exposure31. Short-term, high-level exposure to PM0.1, such as through diesel exhaust, also causes lung inflammation32.

The respiratory mucociliary apparatus is a major tool to clear inhaled particles. Although ultrafine particles can be trapped in the mucous layer, its role in clearance is far less than that for PM of greater density, which impacts the airway. Many lung conditions impair mucociliary function. Ciliary dysfunction is common in smokers and those with respiratory tract infections and may account for the greater vulnerability of these individuals to air pollution. Bronchospasm and cough, which are part of asthma, are common reactions to inhaled irritants, which may account for the increased sensitivity in persons with asthma.

Particulate air pollution is a well-known cause of exacerbations and mortality in persons with chronic obstructive pulmonary disease (COPD), but the role of PM0.1 is unclear. A study from Scotland did not find PM0.1 to be more harmful than PM10 33, but other studies have reported that indoor biological PM0.1 in the form of bacterial extracellular vesicles do cause inflammation and emphysema34.

Ambient exposure to PM0.1 is associated with cough, reduced peak expiratory flow35, and the increased use of medicines36 and hospital admissions for persons with asthma37. Clinical visits for respiratory illness are associated with increased levels of PM0.138. Although most studies have found an increase in asthma symptoms, a study of more than a million adult residents of Toronto did not find evidence for an association between long-term exposure to PM0.1 and respiratory disease after adjusting for PM2.5, NO2, and other covariates39. An Australian controlled study also did not find particle number to be independently associated with respiratory symptoms, asthma diagnosis, or lung function, although PM0.1 was associated with an increase in inflammatory markers in atopic participants40.


Many studies have shown that PM causes systemic inflammation and coagulation changes predisposing to ischemic cardiovascular disease, as measured by elevated C-reactive protein (CRP), circulating polymorphonuclear leukocytes, platelets, fibrinogen, plasma viscosity and other markers. PM promotes endothelial dysfunction, vascular inflammation, and atherosclerosis1. Past studies have attributed this effect mainly to PM2.5, but a growing body of literature shows that PM0.1 have a major role in essentially all of these factors41,42,43. In fact, most studies show a far greater effect for PM0.1. PM0.1 also cause increased heart rate variability, loss of sympathovagal balance, and altered inflammatory and hemostatic function in exposed humans44.

Even brief exposures to PM0.1 can cause cardiac effects. In middle-aged individuals with metabolic syndrome, exposure to PM0.1 for 2 h caused electrocardiographic changes, a decrease in blood plasminogen and thrombomodulin and an increase in CRP and serum amyloid A45.

Many studies have shown an association between chronic exposure to PM0.1 and heart disease. A prospective study of 33,831 Dutch residents found that long-term exposure to PM0.1 (measured by land use regression) was associated with an increased risk for cardiovascular disease, myocardial infarction, and heart failure46. In adults living in Toronto from 1996 to 2012, an increase in PM0.1 exposure was associated with an increased incidence of heart failure and acute myocardial infarction. Adjustment for PM2.5 and NO2 did not change these associations, although NO2 was also independently associated with increased heart failure incidence47. Mobile neighborhood monitoring found the annual average particle number exposures to be associated with stroke, ischemic heart disease, and hypertension48. Other studies have also found increased ischemic and thrombotic stroke with PM0.1 exposure49 and increased blood pressure and worse microvascular function with PM0.1 but not with PM2.5 and PM1043,50.

Particle size has been correlated with total and cardiovascular mortality, with the correlation becoming stronger as the particle size decreases. PM <0.50 µm had the highest correlation9,51. No association was found for mass concentrations (PM2.5 and larger)51.

Particle numbers are associated with cardiovascular disease-related emergency department visits, with a lag of 4–10 days; 10–50 nm particles mainly account for this finding. PM0.1 were reported to account for more than 7% of emergency department visits52. The strongest correlate of immediate effect (within 2 days) was found with 30–100-nm particles, despite a small mass concentration. The immediate effect related to mass concentration was with the 1–5 µm particles, which had a similar delayed effect to the PM0.1 number52.

A study of more than 100,000 women in California found that mortality from ischemic heart disease was more strongly associated with PM0.1 than with PM2.553. Repeated biweekly submaximal exercise tests on adult subjects with stable coronary heart disease showed that PM0.1 were associated with electrocardiographic ST-segment depression of >0.1 mV. The researchers found that the PM0.1 effect was independent of PM2.5. NO2 and CO were also associated with a risk for ST-segment depression, but coarse particles (PM10–2.5) were not54.

However, a study from Denmark of 6515 airport workers who were exposed to long-term PM0.1 found no correlation with ischemic heart disease or cerebrovascular disease compared to the corresponding measures in a similar group of unskilled workers55.

Central nervous system

Many articles have been published on the brain or neural effects of PM, and there is a great deal of animal work on the mechanisms by which PM0.1 affect the brain and its development. Translocated PM0.1 can be found in the brain within 4–24 h after inhalation. Nasal PM0.1 can travel up the olfactory nerves to the brain. Animals exposed to aerosols of PM0.1 have the greatest brain uptake in the olfactory bulb, even 7 days after exposure. In an animal inhalation study, up to 20% of the PM0.1 deposited on the olfactory mucosa moved to the olfactory bulb56. This pathway, which could circumvent the blood brain barrier, may be even more direct in humans57. PM0.1 not only translocate and directly damage neural tissue but also affect autonomic function. Exposure to PM0.1 increases sympathetic nervous system activity by decreasing norepinephrine clearance, a feature that is increased with concurrent ozone (O3) exposure58.

Considerable animal research has been carried out on the effect of PM0.1 on brain development. Postnatally, PM0.1-exposed animals show short-term memory impairment, cortical and hippocampal changes, which raise the potential for excitotoxicity, and long-term glial activation, which is associated with a wide range of behavioral and other neurologic effects59. Pregnant mice administered carbon black nanoparticles intranasally gave birth to offspring with a dose-dependent, long-term activation of astrocytes. Many mRNA level changes associated with angiogenesis, cell migration, proliferation, chemotaxis, and growth factors caused the authors to speculate that this exposure could have wide-ranging implications for health in later life60. Other animal studies have shown that PM0.1 affects emotional behavior, learning capability, neurotransmission, spontaneous motor activity, and avoidance of performance61.

In humans, regular exercise has been shown to improve brain cognition and memory. One mechanism for this effect may be by upregulating brain-derived neurotrophic factor (BDNF). BDNF was measured in subjects before and after cycling for ~20 min near major traffic and, on another occasion, in a room with air filtered to remove PM0.1 as well larger PM. The average PM0.1 was 28,180 particles/cm3 near the road and 496 particles/cm3 in the air-filtered room. Serum BDNF concentration rose after cycling in the air-filtered room but not after cycling near the major traffic route62.


Children are more vulnerable to the health effects of air pollution, and these effects may begin with in utero exposure and have lifelong consequences1. Exposure of pregnant women to PM0.1 increases the risk of low birthweight, especially in those living within 50 m of heavy traffic63.

A study from Ghana monitored the personal exposure of 61 junior high school students 24 h per day for 10 weeks. The exposures varied greatly depending on place of residence and the type of activities in which the students were engaged. The highest exposures were in a home near a trash burning site, in a bedroom with burning coils employed to abate mosquitos, in a home with an adult smoker, and in home kitchens during domestic cooking64. A similar study conducted in the Pearl River delta in China that monitored school children (aged 9–13) for 2 weeks found that the highest exposures were indoors, associated with smoking adults and the use of mosquito repellent incense65. These studies show that the sources of PM0.1 are not always predictable and are not only related to vehicular traffic. Microenvironments and chance exposure have important implications for epidemiologic studies.

A major source of PM0.1 for children living in rural areas can be exhaust from school buses, especially if they are older diesel-powered vehicles. Filtration of the inside air in school buses has been shown to significantly decrease the number of in-cabin ultrafine particles66. Exposure also occurs when children are in the playground and standing outdoors while waiting to enter the bus. Idling engines produce more PM0.1 than driving does67. These exposures can be reduced by anti-idling policies.

Electronic cigarettes are now commonly used by children and are a source of inhaled PM0.168. Electronic cigarettes use heated vehicles (usually propylene glycol and glycerol) to deliver microaerosols to the lungs. They also deliver PM0.1 to the brain along with nicotine. High-resistance coils in electronic cigarettes and increased glycerol generate larger particles, and higher coil temperatures generate smaller particles. Particles produced by the electronic cigarettes are deposited in alveoli69.


Air pollution affects many metabolic functions and has been associated with diabetes and other metabolic illnesses. Exposure to PM0.1 and NO2 from traffic-related sources increases the risk for hypertension and diabetes70. A single 2-h inhalation of elemental carbon PM0.1 had an effect on heart variability in diabetic subjects that lasted for hours71. PM0.1 cause autonomic dysfunction72 and affect glucose tolerance in patients with diabetes73.


Many studies in animals and human cells have shown that PM is mutagenic and tumorigenic61, and it appears that the finer the particle size, the greater the mutagenic potential74. PM0.1 from the atmosphere and roadside contain many mutagenic particles75. PM0.1 have been shown to produce tumors in rats. The strongest tumorigenic factor was the total surface area of the retained particles, although the dose, particle type, and duration of exposure were also important. Smaller aggregated ultrafine TiO2-induced lung tumors in rats much more than larger sized TiO222. The carcinogenic properties of nanoparticles are related to their aspect ratio and rigidness76.


The potential for PM0.1 to cause harm to health is great, but their precise role in many illnesses is still unknown. Their high point-source production and rapid redistribution make incidental exposure common for the general population and confound general population studies. This has, no doubt, contributed to the lack of global standards and national reporting. The absence of standards and reporting may account for the dearth of standardized measurements, instruments, and protocols. Air pollution is a silent epidemic77, and PM0.1 may be the quietest of the pollutants. PM0.1 vary greatly with the toxins they adsorb, adding complexity to public research. In many ways, the study of PM0.1 is at the frontier of air pollution research. As they are better understood, these particles should be more easily controlled. PM0.1, as with other air pollution, are avoidable and correctable health risks. Halting or reducing pollution should promptly result in improved health status78. Undoubtedly, more research is needed.