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from Wikipedia
The SMOG grade is a measure of readability that estimates the years of education needed to understand a piece of writing. SMOG is an acronym for "Simple Measure of Gobbledygook".
SMOG is widely used, particularly for checking health messages.[1][2] The SMOG grade yields a 0.985 correlation with a standard error of 1.5159 grades with the grades of readers who had 100% comprehension of test materials.[3]
The formula for calculating the SMOG grade was developed by G. Harry McLaughlin as a more accurate and more easily calculated substitute for the Gunning fog index and published in 1969. To make calculating a text's readability as simple as possible an approximate formula was also given — count the words of three or more syllables in three 10-sentence samples, estimate the count's square root (from the nearest perfect square), and add 3.
A 2010 study published in the Journal of the Royal College of Physicians of Edinburgh stated that “SMOG should be the preferred measure of readability when evaluating consumer-oriented healthcare material.” The study found that “The Flesch-Kincaid formula significantly underestimated reading difficulty compared with the gold standard SMOG formula.”[4]
Applying SMOG to other languages lacks statistical validity.[5]
Formulae
[edit]To calculate SMOG Index
- Take three ten-sentence-long samples from the text in question.
- In those sentences, count the polysyllables (words of 3 or more syllables).
- Calculate using
This version (sometimes called the SMOG Index) is more easily used for mental math:
- Count the number of polysyllabic words in three samples of ten sentences each.
- Take the square root of the nearest perfect square
- Add 3
SMOG conversion tables compiled by Harold C. McGraw are slightly inaccurate because they are based on the approximate formula. Furthermore, tables for texts of fewer than 30 sentences are statistically invalid, because the formula was normed on 30-sentence samples.
References
[edit]- ^ Hedman, Amy S. (January 2008). "Using the SMOG formula to revise a health-related document". American Journal of Health Education. 39 (1): 61–64. doi:10.1080/19325037.2008.10599016. S2CID 72389214. Retrieved 2009-01-19.
- ^ Ley, P.; T. Florio (February 1996). "The use of readability formulas in health care". Psychology, Health & Medicine. 1 (1): 7–28. doi:10.1080/13548509608400003.
- ^ McLaughlin, G. Harry (May 1969). "SMOG Grading — a New Readability Formula" (PDF). Journal of Reading. 12 (8): 639–646. Retrieved 2018-04-26.
- ^ Fitzsimmons, P.; Michael, B.; Hulley, J.; Scott, G. (2010). "A readability assessment of online Parkinson's disease information". J R Coll Physicians Edinb. 40 (4): 292–6. doi:10.4997/JRCPE.2010.401. PMID 21132132.
- ^ Contreras, A.; Garcia-alonso, R.; Echenique, M.; Daye-contreras, F. (1999). "The SOL Formulas for Converting SMOG Readability Scores Between Health Education Materials Written in Spanish, English, and French". Journal of Health Communication. 4 (1): 21–29. doi:10.1080/108107399127066. PMID 10977275.
from Grokipedia
Smog is a portmanteau of "smoke" and "fog," referring to a visible atmospheric haze resulting from air pollution, typically formed by the mixture of smoke, particulate matter, and chemical pollutants with moisture or through photochemical reactions.[1] It manifests as reduced visibility and can pose severe health risks, primarily due to emissions from fossil fuel combustion in industrial, vehicular, and residential activities.[2]
The two main types of smog are classical (or sulfurous) smog, which arises in cooler, humid conditions from sulfur dioxide, soot, and particulates emitted by coal burning, leading to acidic aerosols; and photochemical smog, which develops in sunny, warmer environments through the ultraviolet-initiated oxidation of nitrogen oxides (NOx) and volatile organic compounds (VOCs) to form ground-level ozone, peroxyacyl nitrates, and secondary particulates.[3][4] Classical smog episodes, such as the 1952 Great Smog of London, trapped pollutants under thermal inversions, causing an estimated 4,000 to 12,000 excess deaths from respiratory and cardiovascular complications.[5][6] Similarly, the 1948 Donora smog event in Pennsylvania resulted in 20 direct deaths and widespread illness among 6,000 residents due to concentrated industrial emissions.[7]
Photochemical smog formation involves a chain of radical reactions: sunlight photodissociates NO2 to nitric oxide and oxygen atoms, which react with O2 to form ozone; ozone then initiates oxidation of VOCs, producing hydroxy radicals that propagate further NOx cycling and secondary pollutant buildup, exacerbating urban air quality in high-traffic areas.[8][9] Health impacts include irritated airways, reduced lung function, aggravated asthma, and increased premature mortality, with vulnerable groups such as children and the elderly most affected; globally, air pollution including smog contributes to millions of deaths annually.[10][11] These events spurred empirical advancements in air quality monitoring and emission controls, underscoring causal links between anthropogenic pollutants and atmospheric visibility degradation.[2]
[135][136][137]
These disparities reflect differences in emission profiles, meteorology, and policy stringency, with developing Asian megacities bearing the brunt of uncontrolled growth versus regulated declines in the West.[154]
Definition and Characteristics
Etymology and Terminology
The term "smog" originated as a portmanteau of "smoke" and "fog," coined in 1905 by British physician Dr. Henry Antoine Des Voeux to characterize the dense, smoke-laden fog prevalent in industrial London.[12][13] Des Voeux introduced the word in his paper "Fog and Smoke," presented at a Public Health Congress, where it received acclaim for succinctly capturing the irritant haze formed by coal combustion emissions mixing with natural fog.[14] This neologism drew inspiration from earlier portmanteau coinages, such as those by Lewis Carroll, and quickly entered usage to denote visible air pollution reducing atmospheric clarity.[12] In terminology, "smog" broadly denotes a suspension of airborne particulates and gases that impairs visibility and arises from anthropogenic emissions interacting with meteorological conditions like fog or inversion layers.[15] Distinct subtypes emerged with scientific understanding: classical or sulfurous smog, termed "London smog" after its association with the 1952 Great Smog event, features high levels of sulfur dioxide (SO₂), particulate matter, and sulfuric acid aerosols primarily from fossil fuel burning in cold, humid environments.[16] In contrast, photochemical smog, also known as "Los Angeles smog," refers to secondary pollutants like ground-level ozone and peroxyacyl nitrates formed via sunlight-driven reactions between nitrogen oxides (NOₓ) and volatile organic compounds (VOCs) from vehicle exhaust and industrial sources, typically under warm, stable atmospheric conditions.[16][17] These classifications, formalized in mid-20th-century air quality research, highlight causal differences in composition and formation rather than mere visual opacity.[1]Physical and Chemical Properties
Smog manifests as a visible haze due to the suspension of fine aerosols and gases in the lower atmosphere, primarily impairing visibility through light scattering and absorption.[18] Aerosol particles, typically in the size range of 0.1 to 10 micrometers, dominate visibility reduction via Mie scattering, where particle diameters approximate visible light wavelengths (0.4–0.7 μm), efficiently backscattering light toward the observer.[19] Gaseous components contribute minimally to scattering but absorb specific wavelengths, with overall extinction coefficients increasing proportionally to pollutant concentrations, often reducing horizontal visibility to below 1 km in dense smog.[20] Physically, smog aerosols exhibit variable density and hygroscopicity, with particles absorbing water vapor to form larger droplets under high humidity, exacerbating opacity; dry densities range from 1–2 g/cm³ for soot and sulfates.[21] The mixture's optical depth correlates with particulate loading, where secondary aerosols from gas-to-particle conversion amplify light attenuation over primary emissions alone.[22] Chemically, smog comprises a heterogeneous blend of primary and secondary pollutants, including particulate matter (PM) such as black carbon, sulfates, nitrates, and organics, alongside gases like sulfur dioxide (SO₂), nitrogen oxides (NOₓ), volatile organic compounds (VOCs), and ozone (O₃).[23] PM₂.₅ fractions (<2.5 μm) predominate in inhalation risks and visibility effects, formed via nucleation, condensation, and coagulation of precursors like SO₂ oxidizing to sulfuric acid aerosols or NOₓ and VOCs photolyzing to secondary organic aerosols.[24] Reactive species enable chain reactions, such as NO₂ photodissociation producing O₃ and radicals that propagate oxidant formation, with equilibrium dictated by temperature, sunlight, and NOx/VOC ratios.[25] Acidic components, including sulfuric and nitric acids, lower pH in droplets, influencing deposition and further chemistry.[26]Historical Development
Early Observations and Events
Awareness of urban smoke pollution predating modern smog emerged in 13th-century London, where King Edward I issued a proclamation in 1272 banning the burning of sea coal due to its offensive odors and effects on air quality, enforced with harsh penalties including execution for repeat offenders.[27] This reflected early empirical recognition of coal combustion's role in degrading atmospheric conditions, though without the fog-smoke mixture defining smog. A detailed early observation came in 1661 with John Evelyn's pamphlet Fumifugium, which documented the pervasive "Cloud or Frog" of soot-laden air from London's coal fires, causing eye irritation, respiratory distress, and damage to vegetation and architecture. Evelyn attributed the haze to excessive sea-coal use for heating and industry, proposing causal remedies like banning coal in the city core, relocating polluting trades, and creating green belts of trees to absorb emissions.[28][29] Presented to King Charles II, the work highlighted first-principles links between anthropogenic emissions and visible air degradation, influencing later environmental thought despite limited immediate policy impact. In the 19th century, during the Industrial Revolution, London's natural fogs increasingly combined with sulfurous coal smoke to form dense "pea-souper" smogs, exacerbating health risks as coal consumption surged to power factories and homes. Observations by chemists like Robert Angus Smith in the 1850s quantified acidic pollutants in Manchester's atmosphere and rainwater, establishing causal connections to coal burning and respiratory ailments.[30] These events correlated with elevated mortality; detailed records from 1866 onward show fog episodes trapping emissions and spiking deaths, with severe instances in the 1870s and 1880s linked to hundreds of excess fatalities from bronchitis and pneumonia.[31][32] Similar smoggy fogs occurred in other industrializing cities like New York, underscoring the pattern of urban emissions amplifying natural weather to produce hazardous air.[32]Key Incidents and Responses
One of the earliest documented severe photochemical smog episodes occurred in Los Angeles on July 26, 1943, when a dense haze reduced visibility to three blocks, caused eye irritation, and produced a bleach-like odor affecting residents.[33] This event, amid wartime industrial activity and vehicle emissions trapped by coastal inversions, prompted the Los Angeles County Board of Supervisors to form a Smoke and Fumes Commission, leading to initial regulations on industrial emissions and the establishment of the Los Angeles County Air Pollution Control District in 1946.[34] Research by chemist Arie Haagen-Smit subsequently identified photochemical reactions between sunlight, nitrogen oxides, and volatile organic compounds from automobiles as the cause, influencing early air quality monitoring and controls.[35] In October 1948, the Donora smog disaster in Donora, Pennsylvania, trapped industrial emissions from zinc works and steel mills in a temperature inversion over the Monongahela River valley from October 26 to 31, resulting in 20 deaths and respiratory illnesses among over 6,000 of the town's 14,000 residents.[36] The incident, exacerbated by sulfur dioxide and particulate matter, highlighted industrial pollution risks and spurred public health investigations, though immediate regulatory responses were limited; it contributed to national awareness that informed the U.S. Air Pollution Control Act of 1955 and later the Clean Air Act of 1970.[37] The Great Smog of London from December 5 to 9, 1952, involved a dense inversion layer trapping sulfurous emissions from coal burning in homes and industries, causing visibility under 100 meters and leading to an estimated 4,000 excess deaths initially reported by government pathologists, with later analyses suggesting up to 12,000 total fatalities from respiratory and cardiovascular issues. This classical smog event, fueled by high-sulfur coal during cold weather, prompted the UK Parliament to pass the Clean Air Act of 1956, which prohibited dark smoke emissions, established smokeless zones, and subsidized cleaner fuels, significantly reducing coal-related pollution in urban areas.[38] Subsequent enforcement and the shift to natural gas via the "smog must go" campaigns marked a pivotal regulatory response to anthropogenic smog formation.[39]Types and Mechanisms
Classical (Sulfurous) Smog
Classical sulfurous smog, also known as London-type or reducing smog, arises primarily from the combustion of sulfur-rich fossil fuels like coal, releasing sulfur dioxide (SO₂) and particulate matter into the atmosphere under conditions of high humidity and temperature inversions.[40] This type of smog is characterized by a high concentration of SO₂, soot, and other fine particulates that combine with fog to form a dense, acidic haze reducing visibility to near zero and irritating respiratory tracts.[41] Unlike oxidizing photochemical smog, it predominates in cooler, overcast winter weather in industrial regions, where stagnant air traps pollutants close to the ground.[42] The formation mechanism begins with anthropogenic emissions of SO₂ from coal-fired power plants and domestic heating, which oxidizes in the presence of oxygen and catalysts like particulate matter to form sulfur trioxide (SO₃). SO₃ then reacts with atmospheric water vapor to produce sulfuric acid aerosols (H₂SO₄), enhancing the hygroscopic nature of existing fog droplets and leading to the growth of secondary particulates.[23] These aerosols, often including black carbon and fly ash, absorb additional gases and contribute to the smog's yellowish-brown tint and corrosiveness, with SO₂ concentrations during episodes exceeding 1-2 ppm and particulate levels surpassing 3 mg/m³.[43] A pivotal historical instance occurred during the Great Smog of London from December 5 to 9, 1952, when an anticyclone and cold snap prompted widespread coal burning, trapping emissions in a shallow inversion layer approximately 100 meters thick. SO₂ levels reached up to 3.7 mg/m³ and smoke concentrations hit 4.5 mg/m³, resulting in an estimated 4,000 to 12,000 excess deaths primarily from respiratory and cardiovascular failures exacerbated by the acidic particulates.[44] [45] This event, analyzed retrospectively through medical records and air quality data, demonstrated the acute lethality of sulfurous smog, with mortality rates spiking 10-fold among those with pre-existing conditions like bronchitis.[43] The 1952 episode catalyzed regulatory responses, including the UK's Clean Air Act of 1956, which restricted sulfurous fuel use in urban areas and mandated smokeless zones, reducing such incidents by promoting cleaner fuels and taller stacks.[39] Similar sulfurous smog events have been documented in other coal-dependent cities, such as the 1930 Meuse Valley fog in Belgium with 60 deaths linked to SO₂ and particulates, underscoring the causal role of high-sulfur emissions in inversion-trapped atmospheres.[46] Empirical monitoring post-regulation confirms that curbing SO₂ emissions directly mitigates classical smog formation, as evidenced by declining winter haze episodes in Europe following desulfurization technologies.[40]Photochemical Smog
Photochemical smog, also known as Los Angeles-type smog, arises from photochemical reactions between primary pollutants—nitrogen oxides (NOx) and volatile organic compounds (VOCs)—under ultraviolet sunlight, producing secondary pollutants such as ground-level ozone (O3), peroxyacetyl nitrate (PAN), and various aldehydes.[4][47] Unlike classical sulfurous smog, which is reducing and prevalent in cool, humid conditions with high sulfur dioxide content, photochemical smog is oxidizing and forms in warm, dry, sunny climates with stagnant air masses, often exacerbated by temperature inversions that trap pollutants near the ground.[48][49] The primary precursors, NOx (emitted mainly as NO from high-temperature combustion in vehicles and power plants) and VOCs (from evaporative emissions, incomplete combustion, and industrial solvents), undergo a chain of radical-initiated reactions initiated by sunlight. NO2 photolyzes to NO and atomic oxygen, which combines with O2 to form O3; VOCs generate peroxy radicals that oxidize NO back to NO2, sustaining ozone production and leading to the characteristic brownish haze.[50][51] Ground-level ozone, the dominant secondary pollutant, peaks in the afternoon due to cumulative reactions, with concentrations often exceeding health standards in urban basins like Los Angeles or Mexico City.[52] First prominently observed in Los Angeles during July 1943, when wartime industrial activity and vehicle exhaust under sunny conditions caused widespread eye irritation and visibility reduction to three blocks, photochemical smog prompted the formation of the Los Angeles County Air Pollution Control District in 1947, the first such agency in the United States.[53][54] Dutch chemist Arie Haagen-Smit at Caltech demonstrated in the early 1950s that smog formation required both NOx and hydrocarbons irradiated by sunlight, shifting focus from simple particulate matter to gas-phase photochemistry.[55] This type of smog remains prevalent in megacities with heavy traffic and topography that hinders dispersion, such as the Los Angeles Basin, where ozone levels historically reached 0.68 ppm in the 1950s before regulatory interventions reduced peak concentrations by over 90% by 2020 through NOx and VOC controls.[53]Formation Processes
Sulfurous smog, also known as classical or London-type smog, forms through the oxidation of sulfur dioxide (SO₂) emitted primarily from the incomplete combustion of sulfur-rich fossil fuels such as coal. In cool, humid atmospheric conditions—typically with temperatures below 10°C and relative humidity above 70%—SO₂ undergoes catalytic oxidation on the surface of particulate matter like soot or metal aerosols to sulfur trioxide (SO₃), via reactions such as 2SO₂ + O₂ → 2SO₃. The SO₃ then rapidly reacts with water vapor to produce sulfuric acid mist (H₂SO₄ droplets): SO₃ + H₂O → H₂SO₄. These acidic aerosols condense onto existing particulates, forming a reducing haze that impairs visibility; temperature inversions exacerbate this by trapping the mixture near the ground.[56][42] Photochemical smog, or Los Angeles-type smog, develops via sunlight-driven chain reactions involving nitrogen oxides (NOₓ) and volatile organic compounds (VOCs) or hydrocarbons, precursors from vehicle exhaust and industrial emissions. Ultraviolet radiation photolyzes nitrogen dioxide (NO₂) to nitric oxide (NO) and atomic oxygen (O): NO₂ + hν → NO + O, followed by O + O₂ + M → O₃ + M (where M is a third-body molecule stabilizing the ozone). This initiates radical propagation: VOCs react with hydroxyl radicals (OH•) to form peroxy radicals (RO₂•), which oxidize NO back to NO₂, sustaining ozone production and generating secondary pollutants like peroxyacetyl nitrate (PAN) through RO₂• + NO₂ → RO₂NO₂. These processes dominate in warm, sunny conditions (temperatures above 20°C) with low wind speeds, favoring high oxidant levels and aerosol formation over hours to days.[57][58] Both types require stagnant air masses, often under inversion layers where warmer air aloft prevents vertical mixing, concentrating precursors; however, sulfhurous smog prevails in winter with high SO₂ emissions, while photochemical smog peaks in summer due to abundant solar radiation and biogenic VOC contributions from vegetation. Empirical measurements, such as those from chamber simulations, confirm that radical cycling efficiency depends on NO₂/NO ratios and VOC reactivity, with peer-reviewed models showing ozone yields increasing nonlinearly with precursor ratios above 8:1 (NOₓ:VOC by mass).[59][60]Causes and Contributors
Anthropogenic Sources
Anthropogenic sources of smog primarily involve emissions of precursor pollutants such as sulfur dioxide (SO₂), nitrogen oxides (NOₓ), volatile organic compounds (VOCs), and particulate matter (PM) from human activities, which dominate urban air pollution concentrations compared to natural contributions in most developed regions.[61] These emissions arise mainly from incomplete combustion of fossil fuels and industrial processes, leading to both classical sulfurous smog and photochemical smog formation under specific meteorological conditions.[62] Transportation, particularly on-road vehicles, accounts for a significant portion of NOₓ and VOC emissions, key precursors to photochemical smog via ground-level ozone production. In the United States, mobile sources contribute approximately 25-30% of total NOₓ emissions, with passenger cars, trucks, and buses emitting hydrocarbons and nitrogen oxides during fuel combustion.[2] Diesel engines in heavy-duty vehicles further add to primary PM emissions, exacerbating visibility reduction and secondary aerosol formation.[63] Electric power generation and industrial facilities are major emitters of SO₂ and NOₓ, fueling classical smog episodes historically linked to coal-fired plants. Coal combustion in power plants releases SO₂ through sulfur content in fuel, with global anthropogenic SO₂ emissions exceeding 80 million metric tons annually as of recent inventories, predominantly from energy production (about 50%) and industry (30%).[61] Refineries and metal smelters contribute additional SO₂ and PM via high-temperature processes, while chemical manufacturing emits VOCs from solvents and petrochemical handling.[64] Residential and commercial heating, often using coal, oil, or biomass, generates PM and SO₂, particularly in developing regions where solid fuel use persists. In Europe and North America, these sources have declined due to fuel switching, but they remain relevant in episodic smog events during winter inversions.[65] Industrial solvent use and evaporation from fuel storage also supply VOCs, reacting with NOₓ in sunlight to form secondary organic aerosols integral to haze.[66] Overall, sector contributions vary by region, with transportation dominating in urban photochemical smog and energy/industry in sulfurous cases, as evidenced by emission inventories from agencies like the EPA.[67]Natural Sources
Natural sources contribute smog-forming pollutants through episodic emissions of sulfur dioxide (SO₂), particulate matter (PM), volatile organic compounds (VOCs), and nitrogen oxides (NOx), which can react under specific atmospheric conditions to produce haze, sulfate aerosols, or ground-level ozone.[68] Unlike persistent anthropogenic emissions, these natural contributions are often transient and regionally dominant during events like eruptions or fires, though they generally play a secondary role in chronic urban smog.[69] Biogenic emissions from vegetation represent a continuous but diffuse source, while geological and pyrogenic events provide acute inputs.[24] Volcanic eruptions release substantial SO₂—up to millions of tons per major event—which oxidizes in the presence of sunlight, oxygen, and moisture to form sulfuric acid aerosols, creating "volcanic smog" or vog, a bluish haze resembling photochemical smog.[70] For instance, ongoing emissions from Hawaii's Kīlauea volcano since 1983 have produced vog that disperses hundreds of kilometers, irritating respiratory systems and reducing visibility.[71] Globally, volcanoes contribute about 20-25 teragrams of sulfur to the atmosphere annually, influencing sulfate PM levels, though this is dwarfed by human sources in industrialized regions.[72] Wildfires, ignited by lightning or natural dry conditions, emit dense smoke plumes containing PM2.5 (fine particles under 2.5 micrometers), black carbon, VOCs, and NOx, which can travel thousands of kilometers and exacerbate regional smog by promoting secondary aerosol and ozone formation.[73] In 2023, wildfires in Canada released over 1.5 billion tons of carbon equivalent, generating transboundary haze that degraded air quality across the northeastern United States, with PM2.5 concentrations exceeding 100 μg/m³ in affected cities.[74] These events contribute up to 60% more carbon emissions from fires globally since pre-industrial times, intensifying short-term smog episodes in fire-prone ecosystems like boreal forests.[75] Biogenic VOCs (BVOCs), primarily isoprene and monoterpenes emitted by trees and plants, total around 1,000 teragrams per year worldwide and serve as precursors to photochemical smog by reacting with NOx under sunlight to yield ozone and secondary organic aerosols.[76] In vegetated areas with low anthropogenic NOx, such as rural or forested regions, BVOCs can drive up to 50% of summertime ozone formation, as observed in the southeastern United States where oak and pine emissions peak in warm conditions.[77] These compounds enhance aerosol formation, contributing to hazy conditions, though their impact diminishes in high-NOx urban environments where human VOCs dominate.[78] Other minor natural sources include wind-blown dust from arid regions, which adds coarse PM and can transport minerals over continents, and sea spray aerosols generating chloride particles that influence coastal haze.[79] Dust storms, such as those from the Sahara, loft billions of tons of PM annually, occasionally merging with smoke to form widespread smog layers, but their chemical reactivity is lower than that of gaseous precursors.[80] Overall, while natural sources episodically rival or exceed anthropogenic pollution in remote areas, their global contribution to persistent smog remains limited by lack of sustained emissions.[62]Relative Contributions and Debates
Anthropogenic activities, particularly fossil fuel combustion in transportation (accounting for 20-30% of NOx emissions globally), industry, and power generation, provide the predominant precursors—such as nitrogen oxides (NOx), sulfur oxides (SOx), volatile organic compounds (VOCs), and primary particulate matter (PM)—for both classical and photochemical smog in densely populated regions. Biomass burning, including agricultural residue combustion often classified as anthropogenic, contributes substantially to carbonaceous aerosols and PM2.5, especially in South Asia where it drives seasonal smog episodes.[81] In contrast, natural sources like wildfires, desert dust, volcanic eruptions, and biogenic VOC emissions from vegetation contribute variably, with global estimates indicating natural origins responsible for about 33% of the mortality burden from ambient PM2.5 exposure, primarily through episodic spikes rather than chronic urban haze.[82] For ozone formation in photochemical smog, biogenic VOCs can comprise up to 50-80% of total VOCs in rural or forested areas, interacting with anthropogenic NOx to amplify ground-level concentrations.[83][77] Regional disparities highlight these dynamics: in the United States, anthropogenic sectors like energy (15% of PM2.5-related deaths) overshadow natural contributions outside wildfire seasons, whereas globally, natural dust and sea spray elevate baseline PM2.5 in arid or coastal zones, sometimes exceeding WHO guidelines even in low-emission scenarios.[82][69] Volcanic SO2 and lightning-induced NOx add transient layers to sulfhurous smog, though their annual global input remains below anthropogenic levels at roughly 10-20% for SOx.[84] Secondary organic aerosols from natural terpenes further complicate attribution, as they form via oxidation processes akin to those from human-emitted VOCs.[77] Debates persist over partitioning these contributions, particularly in air quality modeling and policy, where overreliance on anthropogenic inventories may undervalue natural baselines, leading to unattainable standards in regions with persistent dust or biogenic influences—MIT analyses suggest over 50% of the global population would face PM2.5 exceedances from natural sources alone under stringent guidelines.[69] Critics argue that episodic natural events, such as intensified wildfires linked to land management rather than solely emissions, are sometimes conflated with chronic human pollution, skewing regulatory focus; peer-reviewed assessments emphasize integrating both for accurate forecasting, as biogenic-anthropogenic interactions can enhance ozone by factors of 2-3 in urban-vegetated interfaces.[85][77] Conversely, some environmental advocates prioritize anthropogenic controls, citing their controllability despite natural dominance in total PM mass during peaks, underscoring tensions between empirical source apportionment and mitigation feasibility.[79]Impacts
Health Effects
Exposure to smog, particularly its key components such as fine particulate matter (PM2.5), sulfur dioxide (SO2), ground-level ozone (O3), and nitrogen dioxide (NO2), induces acute respiratory irritation, including coughing, wheezing, and shortness of breath, with short-term elevations linked to exacerbations of asthma and chronic obstructive pulmonary disease (COPD).[86] [87] The 1952 Great Smog of London, characterized by high SO2 and PM levels from coal combustion, caused an estimated 12,000 excess deaths over three months, primarily from acute bronchial and pulmonary issues, alongside increased hospitalizations for pneumonia and bronchitis.[88] Similar acute episodes of photochemical smog, rich in O3 and secondary aerosols, have been associated with heightened emergency department visits for respiratory distress.[89] Chronic exposure to smog pollutants contributes to cardiovascular morbidity and mortality, with long-term PM2.5 levels strongly correlated to ischemic heart disease, stroke, and heart failure; epidemiological cohorts show hazard ratios for cardiovascular death rising by 6-13% per 10 μg/m³ increment in PM2.5.[90] [91] Ozone exposure over years elevates risks of respiratory mortality and COPD progression, independent of PM effects.[92] Globally, ambient air pollution—including smog components—accounted for 4.2 million premature deaths in 2019, with 68% attributed to cardiovascular causes like ischemic heart disease and stroke, and 14% to respiratory diseases such as COPD.[93] Vulnerable groups, including the elderly, children, individuals with preexisting cardiopulmonary conditions, and those of lower socioeconomic status, exhibit amplified risks; for instance, PM2.5 exposure disproportionately increases cardiovascular mortality in those with prior heart or lung disease.[94] Recent studies (2020-2024) confirm that even moderate PM2.5 concentrations (below 10 μg/m³) sustain associations with incident acute myocardial infarction and overall cardiovascular disease mortality.[91] [95] Evidence from toxicological and cohort data supports causal pathways involving systemic inflammation, oxidative stress, and endothelial dysfunction, though debates persist on thresholds below which no effects occur.[86]Environmental and Ecological Effects
Smog, particularly its photochemical variant dominated by ground-level ozone, induces foliar injury in sensitive vegetation by penetrating stomata and oxidizing plant tissues, leading to stippling, necrosis, and premature leaf senescence.[96] This oxidative stress disrupts photosynthesis, reducing carbon assimilation and biomass accumulation in forests, grasslands, and wetlands, with documented yield losses in native species exceeding 10% at seasonal ozone concentrations above 60 parts per billion.[97] Sulfurous smog precursors, such as sulfur dioxide, exacerbate these effects by causing chlorosis and necrosis directly on leaves, while contributing to acid deposition that leaches essential nutrients like calcium and magnesium from forest soils.[98] In aquatic ecosystems, sulfurous smog's role in acid rain formation lowers pH in lakes, streams, and coastal waters, mobilizing toxic aluminum from soils and sediments, which impairs gill function in fish and amphibians, resulting in reproductive failures and population declines.[99] For instance, in regions like the northeastern United States during the 1980s peak, acidification eliminated sensitive fish species from thousands of Adirondack lakes, with recovery lagging despite emission reductions due to persistent soil buffering deficits.[100] Nitrogen oxides from both smog types deposit as wet and dry fallout, eutrophying oligotrophic waters and favoring invasive algae over native flora, which disrupts food webs and reduces biodiversity in estuaries and wetlands.[101] Terrestrial ecological impacts include altered species composition in forests, where ozone-sensitive trees like ponderosa pine exhibit crown thinning and increased susceptibility to pests, accelerating dieback in mixed conifer stands exposed to chronic pollution.[102] Particulate matter from smog settles on foliage, blocking light interception and promoting pathogenic fungi, while acid deposition in high-elevation spruce-fir ecosystems depletes base cations, stunting regeneration and shifting dominance toward tolerant hardwoods.[103] These changes cascade to wildlife, as reduced plant productivity diminishes forage quality, leading to bioaccumulation of pollutants in herbivores and endocrine disruption in predators, with studies linking ozone exposure to impaired avian reproduction and mammalian respiratory pathology.[104] Overall, smog-driven pollution contributes to biodiversity loss by favoring tolerant species and stressing keystone taxa, with meta-analyses indicating negative effects on pollination services from ozone-altered floral signals and pollinator behavior.[105] In polluted corridors, such as urban-adjacent habitats, wildlife corridors fragment due to habitat degradation, amplifying extinction risks for smog-intolerant endemics, though empirical recovery in regulated areas underscores causality tied to emission controls rather than natural variability alone.[106]Economic Consequences
Smog imposes substantial economic burdens through health impairments, lost productivity, and agricultural yield reductions, with particulate matter (PM) from classical smog and ozone from photochemical smog as key drivers. Globally, the health damages from ambient PM2.5—a major smog constituent—were valued at $8.1 trillion in 2019, equivalent to 6.1% of world GDP, encompassing mortality, morbidity, and associated welfare losses.[107] [108] In the United States, outdoor air pollution, including smog episodes, generated damages amounting to roughly 5% of annual GDP, or $790 billion in 2014 terms, primarily via reduced labor supply and increased medical spending.[109] [110] Health costs predominate, stemming from smog-exacerbated respiratory illnesses, cardiovascular events, and premature deaths; for example, PM2.5 and ozone exposures linked to smog contribute to 4.2 million annual premature deaths worldwide as of 2019 estimates.[93] In the US, these effects translate to $820 billion yearly in healthcare expenditures as of 2021, averaging $2,500 per person in medical bills for pollution-attributable conditions.[111] Morbidity from smog-related pollutants also drives productivity declines, with global lost labor income from air pollution mortality reaching $225 billion in 2013 alone.[112] Regional assessments, such as in Utah, peg total annual economic costs of air pollution—including smog—at $0.75 to $3.3 billion, up to 1.7% of state GDP, with indirect losses from absenteeism and reduced work capacity comprising a median $0.9 billion.[113] [114] Agricultural losses arise chiefly from tropospheric ozone in photochemical smog, which damages plant stomata and photosynthesis, reducing global yields of staple crops by 79 to 121 million tonnes annually and inflicting $11 to $18 billion in economic value.[115] In China, ozone pollution correlates with declining agricultural total factor productivity, amplifying food security risks in high-smog regions.[116] Specific episodes, such as in India's Indo-Gangetic Plain, yielded 3.4 million tonnes of wheat losses from ozone exposure in studied districts during recent periods.[117] Classical smog's PM and sulfur dioxide further erode crop health indirectly via soil and visibility effects, though ozone dominates quantified yield impacts.[110] Additional costs include material degradation from smog acidity and particulates, necessitating frequent industrial maintenance and urban infrastructure repairs, though these are secondary to health and agriculture in aggregate valuations.[50] Overall, these consequences reduce GDP growth potential, with projections indicating escalating market costs from labor and crop losses unless pollution levels decline.[110] Empirical analyses consistently show benefits of pollution controls exceeding abatement expenses in 70% of cases, underscoring smog's net drag on economic welfare.[108] [118]Mitigation and Regulation
Technological and Engineering Solutions
Catalytic converters, introduced in automobiles in the mid-1970s, chemically convert harmful exhaust gases such as carbon monoxide (CO), nitrogen oxides (NOx), and volatile organic compounds (VOCs)—key precursors to photochemical smog—into less toxic substances like carbon dioxide (CO2), nitrogen (N2), and water vapor.[119] These devices achieve reduction efficiencies of up to 98% under optimal conditions, significantly contributing to decreased smog formation in urban areas like Los Angeles following their widespread adoption after U.S. Clean Air Act mandates in 1975.[120][119] For stationary sources such as power plants and industrial boilers, selective catalytic reduction (SCR) systems inject ammonia or urea into flue gases to catalytically reduce NOx emissions by over 90%, targeting the nitrogen oxides that drive ozone formation in smog.[121] Implemented widely since the 1980s, SCR technology has been refined for high-temperature operation, with modern systems achieving near-zero NOx tailpipe equivalents in diesel engines and stationary applications.[122] Electrostatic precipitators (ESPs) address particulate matter (PM) from industrial stacks, charging particles electrostatically to collect them on plates, removing up to 99% of fine ash, dust, and soot that contribute to visible smog haze.[123] Deployed in coal-fired power plants since the early 20th century and optimized post-1970 Clean Air Act, ESPs handle high-volume gas streams with minimal pressure drop, though performance depends on factors like particle resistivity and gas composition.[124] Wet and dry scrubbers, engineering variants using chemical absorption or adsorption, capture sulfur dioxide (SO2) and acid gases from emissions, reducing their role in sulfrous smog episodes, with efficiencies exceeding 95% in flue gas desulfurization systems at utilities.[125] These technologies, scaled for large facilities, often integrate with ESPs for multi-pollutant control but require ongoing maintenance to mitigate issues like scaling or reagent consumption.[125] Diesel particulate filters (DPFs), paired with regeneration cycles, trap and oxidize PM from heavy-duty vehicles, cutting black carbon emissions—a smog visibility factor—by 85-99% in modern implementations.[120] Advances in materials like cordierite and silicon carbide have enabled passive and active regeneration, extending filter life in real-world fleets since EPA Tier 4 standards in 2010.[120]Policy and Regulatory Measures
The United Kingdom's Clean Air Act of 1956, enacted following the deadly Great Smog of London in December 1952 which killed approximately 4,000 people, established smoke control areas where only authorized fuels could be burned and prohibited dark smoke emissions from chimneys in urban districts.[126] The Act provided government grants for converting domestic and industrial furnaces from coal to cleaner fuels like coke or gas, significantly curbing sulfur dioxide and particulate emissions responsible for winter smog episodes.[127] In the United States, the Clean Air Act of 1970, as amended in 1977 and 1990, empowers the Environmental Protection Agency (EPA) to set National Ambient Air Quality Standards (NAAQS) for criteria pollutants including ground-level ozone—a key component of photochemical smog—and fine particulate matter (PM2.5), which contributes to haze and visibility-reducing aerosols.[128] States must submit State Implementation Plans (SIPs) to achieve these standards, with non-attainment areas facing stricter controls on volatile organic compounds (VOCs), nitrogen oxides (NOx), and precursors; the 1990 amendments introduced market-based programs like emissions trading for acid rain precursors that indirectly reduced smog-forming SO2.[129] China's Air Pollution Prevention and Control Action Plan, issued by the State Council in September 2013, outlined ten measures targeting PM2.5 reductions through coal consumption controls, stricter vehicle emission standards, and industrial upgrades, aiming for a nationwide improvement in air quality by 2017 with further plans extending reductions in key regions like the Beijing-Tianjin-Hebei area.[130] The European Union's Ambient Air Quality Directive (2008/50/EC) sets binding limits for PM10, PM2.5, NO2, and ozone, requiring member states to monitor exceedances and develop action plans; a revised directive adopted in 2024 halves the annual PM2.5 limit to 10 µg/m³ by 2030, aligning closer to WHO guidelines updated in 2021 recommending 5 µg/m³ for PM2.5.[131][132] India's National Clean Air Programme (NCAP), launched in 2019, targets a 20-30% reduction in PM10 and PM2.5 concentrations by 2024 (extended to 40% by 2026) in 132 non-attainment cities through source apportionment studies, enhanced monitoring, and sector-specific interventions like dust control and vehicular emission norms.[133] These measures often draw on WHO guidelines for pollutant thresholds, though implementation varies by jurisdiction with emphasis on local enforcement of emission standards for power plants, vehicles, and industries to mitigate smog formation.[132]Effectiveness, Costs, and Trade-offs
Mitigation strategies for smog, encompassing both technological interventions and regulatory measures, have demonstrated measurable reductions in key pollutants such as fine particulate matter (PM2.5) and ground-level ozone in regions with stringent implementation. In the United States, the Clean Air Act amendments have contributed to nationwide declines in ambient PM2.5 concentrations by approximately 40% and ozone levels by 25% from 1990 to 2020, correlating with averted premature deaths estimated at 230,000 during that period.[134][135] Similarly, China's national air quality action plans achieved a 10% reduction in annual average PM2.5 concentrations from 2020 levels by 2025, with a 2.7% year-on-year drop in 2024, primarily through controls on industrial emissions and coal combustion.[136][137] These outcomes reflect the efficacy of targeted precursor emission reductions, such as sulfur oxides (SOx) and nitrogen oxides (NOx), though effectiveness varies by pollutant and location; for instance, primary PM2.5 controls yield the most direct impacts compared to volatile organic compound (VOC) management.[138] Economic costs of smog mitigation include direct compliance expenditures for pollution controls, such as scrubbers and catalytic converters, alongside indirect burdens like higher energy prices and industrial retrofits. Retrospective analyses of the U.S. Clean Air Act from 1990 to 2020 estimate aggregate compliance costs at $65 billion annually by 2020, encompassing capital investments and operational expenses across sectors like power generation and transportation.[135] In China, achieving PM2.5 targets through 2025 involved investments exceeding hundreds of billions in yuan for emission controls and fuel switching, with ongoing annual costs for monitoring and enforcement.[139] Systematic reviews indicate that while 70% of studied air pollution control strategies show net positive economic returns when factoring health savings, upfront capital outlays can strain smaller enterprises and delay infrastructure projects.[140] Trade-offs arise from the interplay between air quality gains and economic or secondary environmental effects, including pollutant-specific interactions and sectoral displacements. NOx reductions effectively lower PM2.5 but can elevate ozone concentrations by 20-25% in high-PM urban areas like Delhi if not paired with VOC controls, necessitating balanced multi-pollutant strategies.[141][142] Employment impacts remain debated; while aggregate U.S. data show no substantial net job losses from Clean Air Act regulations, localized effects in manufacturing-heavy regions include plant relocations and productivity dips of up to 1-2% in regulated industries.[143][144] In China, eastern smog reductions have shifted pollution westward, increasing PM2.5 exposure in less-regulated provinces and highlighting transboundary challenges.[145] Overall, health benefits—valued at trillions in avoided mortality and morbidity—typically exceed costs by ratios of 30:1 in EPA assessments, though critics argue these valuations overstate willingness-to-pay metrics and undercount regulatory rigidities that hinder innovation.[135][146]| Aspect | U.S. Clean Air Act (1990-2020) | China Action Plans (2020-2025) |
|---|---|---|
| PM2.5 Reduction | ~40% national average | 10% from 2020 baseline |
| Ozone Reduction | ~25% | Variable, with NOx focus aiding secondary formation control |
| Estimated Costs | $65B/year by 2020 (compliance) | Hundreds of billions yuan (investments) |
| Key Trade-off | Local employment dips in heavy industry | Pollution shift to western regions |
Global Patterns and Trends
Regional Variations
Sulfurous smog, characterized by high concentrations of sulfur dioxide and particulate matter from coal combustion, was historically prevalent in industrial regions of Europe, most notably during the Great Smog of London in December 1952, when black smoke levels reached approximately 4,000 micrograms per cubic meter and sulfur dioxide concentrations exceeded 1,400 micrograms per cubic meter, contributing to an estimated 12,000 excess deaths.[30] Subsequent regulatory measures, including the UK's Clean Air Act of 1956 and broader European Union directives, reduced sulfur oxide emissions by over 84% across Europe since 2005 through fuel switching and flue gas desulfurization, rendering such events rare today with annual PM2.5 averages in cities like London typically below 10 micrograms per cubic meter.[147] [148] In contrast, photochemical smog—formed by reactions between nitrogen oxides, volatile organic compounds, and sunlight—dominates in topographically confined urban areas with heavy vehicular traffic and industrial activity, such as the Los Angeles basin in North America, where inversion layers trap pollutants, leading to ozone levels that frequently exceeded federal standards in the 1970s but have since declined due to catalytic converters and emission controls, with 2023 PM2.5 averages around 9.5 micrograms per cubic meter.[149] [150] Mexico City exhibits similar basin-induced photochemical episodes, compounded by rapid urbanization, resulting in higher PM2.5 concentrations of about 22.3 micrograms per cubic meter in recent years despite vehicle restrictions and fuel reforms implemented since the 1990s.[149] [151] Asia experiences the most severe contemporary smog variations, blending photochemical processes with elevated particulates from coal power, biomass burning, and construction dust; in Beijing, aggressive controls since China's 2013 air pollution action plan lowered PM2.5 from peaks over 80 micrograms per cubic meter to 34.1 micrograms per cubic meter by 2023, though rebounds occurred amid economic recovery post-COVID.[149] [152] Delhi, India, faces acute winter episodes intensified by agricultural stubble burning and Diwali fireworks, yielding annual PM2.5 averages exceeding 100 micrograms per cubic meter—over 20 times the WHO guideline—far surpassing photochemical hotspots elsewhere due to uncontrolled open burning and lax enforcement.[153] [149]| City/Region | Dominant Smog Type | Approx. Annual PM2.5 (µg/m³, 2023) | Key Causes |
|---|---|---|---|
| London (Europe) | Historical sulfurous | <10 | Past coal use; now minimal |
| Los Angeles (North America) | Photochemical | 9.5 | Vehicles, geography |
| Mexico City (Latin America) | Photochemical | 22.3 | Vehicles, industry |
| Beijing (East Asia) | Mixed photochemical/particulate | 34.1 | Coal, vehicles |
| Delhi (South Asia) | Mixed with biomass peaks | >100 | Burning, traffic |