DMSe and DMDSe undergo chemical reactions with O₃ in the atmosphere, which plays a crucial role in their transformation and fate in the atmosphere^[19,42]. The ozonolysis of DMSe proceeds through a mechanism analogous to that of DMS, with the initial formation of a primary ozonide (POZ) intermediate that subsequently decomposes via a Criegee-type pathway. The key steps are as follows:

DMSe + O₃ → [DMSe·O₃]⁺ (primary ozonide) (1a)

[DMSe·O₃]⁺ → CH₃SeO• + •OCH₃ (1b)

CH₃SeO• + O₂ → CH₃SeOO• (1c)

CH₃SeOO• + NO → CH₃SeO• + NO₂ (1d)

The primary pathway yields CH₃SeO• and CH₃SeOO• radicals, which further react with NOx (NO/NO₂) to form stable products such as methylselenyl nitrate (CH₃SeONO₂) and dimethyl selenoxide (DMSeO, CH₃Se(O)CH₃)^[42].

The overall reaction is:

DMSe + O₃ → Dimethylselenoxide (DMSeO) (1)^[42]

For DMDSe, the ozonolysis mechanism involves cleavage of the Se–Se bond, yielding methylseleninic acid (MSeA, CH₃SeO₂H) as the major product:

DMDSe + O₃ → CH₃SeO₂H (MSeA) + CH₃Se• (2)^[42]

The reaction between DMSe and O₃ has a rate constant of 7.4 × 10^-17 cm³·molec^-1·s^-1 at 25 °C under standard atmospheric conditions^[42] [Figure 3A]. The rate is influenced by temperature, humidity, and light; higher temperatures increase the fraction of molecules that surpass the activation barrier, thereby accelerating the reaction. When the O₃ concentration in the atmosphere is 20 ppb, the atmospheric lifetime of DMSe is approximately 7.6 h based on reaction kinetics calculations^[42]. This lifetime estimation considers only O₃ reactions and thus neglects other critical oxidation pathways [e.g., with OH and nitrate radicals (NO₃)], which can significantly shorten the atmospheric lifetime of DMSe. In real-world environments, background aerosols and varying humidity levels can significantly modulate these O₃-driven lifetimes. For instance, in marine boundary layers with high relative humidity (> 80%), the enhanced surface area of deliquescent sea-salt aerosols may facilitate heterogeneous uptake of DMSe, potentially shortening its effective atmospheric lifetime through surface-mediated reactions^[42]. Conversely, in urban environments where aerosol acidity is elevated, the partitioning of oxidation products (e.g., dimethyl selenoxide) into the condensed phase may be accelerated, removing gaseous selenium compounds from the gas phase more rapidly than predicted by homogeneous kinetics alone^[19,20]. In contrast, under dry continental conditions, gas-phase oxidation remains the dominant loss pathway, and the O₃-driven lifetime estimates may better approximate actual atmospheric behavior. These geographical variations underscore the need for integrating heterogeneous chemistry into atmospheric models to refine selenium lifetime predictions across different environmental regimes.

Heine et al. (2023) has elucidated the ozonolysis pathways of DMSe and DMDSe, reporting rate constants of (7.4 ± 2.2) × 10^-17 cm³·molec^-1·s^-1 for DMSe and (2.6 ± 0.9) × 10^-17 cm³·molec^-1·s^-1 for DMDSe at 26 ± 1 and 27 ± 1 °C, respectively^[42]. The activation energies were determined to be 50 ± 14 kJ·mol^-1 for DMSe and 56 ± 5 kJ·mol^-1 for DMDSe^[42]. The primary oxidation product of DMSe was identified as dimethyl selenoxide (CH₃Se(O)CH₃), while the ozonolysis of DMDSe yielded methylselenic acid (CH₃Se(O)OH), likely formed via hydrolysis of the transient anhydride CH₃Se(O)OSe(O)CH₃. These findings demonstrate that DMSe reacts faster with O₃ than DMDSe, consistent with the higher electron density on the Se atom of monoselenides compared to diselenides.

Recent work by Heine et al. (2025) demonstrates the abiotic formation of dimethyl selenyl sulfide (DMSeS) through light-driven reactions in both liquid and gas phases, suggesting its potential role as an intermediate in atmospheric selenium transformations^[36]. This finding highlights a previously overlooked pathway in selenium cycling, where mixed chalcogen species like DMSeS may form via photochemical processes involving DMSe and sulfur-containing compounds. Given its reactivity, DMSeS could serve as a transient species influencing the speciation and fate of atmospheric selenium. This discovery expands our understanding of non-biological selenium chemistry in the environment. The study underscores the need to consider such mixed S-Se species in atmospheric models.

The chemical equation for the reaction between DMDSe and O₃ is:

DMDSe + O₃ → MSeA (2)^[42]

This reaction is relatively slow, with a rate constant of 2.6 × 10^-17 cm³·molec^-1·s^-1[42] [Figure 3B]. This results in a relatively long atmospheric lifetime for DMDSe, approximately 22 h^[42]. The ozonolysis of DMDSe proceeds via a complex mechanism involving multiple intermediates and transition states^[42]. Recent work by Breuninger et al. (2024) confirms that DMDSe can be detected in ambient air, but its atmospheric occurrence appears limited due to its relatively short lifetime of approximately 22 h^[32]. This instability suggests DMDSe is likely a minor contributor compared to more stable selenium compounds like DMSe. The rapid degradation implies that any atmospheric DMDSe measurements would represent localized, recent emissions rather than accumulated background levels. This distinction is important for modeling selenium speciation and understanding its atmospheric cycling. DMSeO and MSeA likely dissolve in droplets because of their polar functional groups. O₃ cleaves the Se–Se bond in DMDSe, ultimately yielding methylseleninic acid through a series of oxidation steps^[42]. Other gaseous species (e.g., NOx, SO₂) may influence this reaction by interacting with reactants or products, thereby altering the pathway and rate^[19].

The hydroxyl radical (OH) is a highly reactive atmospheric oxidant^[43,44]. The DMSe + OH reaction likely proceeds via H-abstraction from the –CH₃ group, forming •CH₂SeCH₃ and H₂O, followed by O₂ addition to yield peroxy radicals (•O₂CH₂SeCH₃)^[45]:

DMSe + •OH → •CH₂SeCH₃ + H₂O (3a)

•CH₂SeCH₃ + O₂ → •O₂CH₂SeCH₃ (peroxy radical) (3b)

•O₂CH₂SeCH₃ + NO → •OCH₂SeCH₃ + NO₂ (3c)

•OCH₂SeCH₃ + O₂ → HCHO + CH₃SeO• (3d)

The peroxy radical (•O₂CH₂SeCH₃) can also undergo isomerization or react with HO₂ to form organic hydroperoxides (CH₃SeCH₂OOH). The overall degradation pathway leads to the formation of formaldehyde (HCHO) and methylseleninic acid (CH₃SeOOH) as stable end products^[45].

DMSe + OH → CH₃SeOOH + HCHO (3)^[45]

Subsequent reactions may include RO₂ + NO or isomerization, analogous to DMS + OH pathways, forming stable intermediates such as formaldehyde (HCHO) and methylselenic acid (CH₃SeOOH)^[45]. The reaction rate between DMSe and OH is relatively high^[45]. Electron transfer is not a significant pathway; instead, radical-driven chain reactions dominate, as demonstrated for analogous sulfur compounds^[43]. The OH-initiated oxidation of DMSe proceeds with a rate constant (k = 6.8 × 10^-10 cm³·molec^-1·s^-1), ~30% faster than DMS (k = 8.5 × 10^-12 cm³·molec^-1·s^-1), implying a shorter atmospheric lifetime (~5 h vs. ~1 day for DMS under typical [OH] = 1 × 10⁶ molec·cm^-3). This difference arises from weaker C–Se bonds and enhanced radical stabilization in selenium intermediates^[45]. Under pseudo-first-order kinetics, the OH-dominated atmospheric lifetime of the compound is approximately 1.5 h (assuming [OH] = 1 × 10⁶ molec·cm^-3), while the O₃-dominated lifetime is 7.6 h. The combined effective lifetime is 1.3 h, indicating OH radicals dominate the degradation process^[7,42,45]. Due to the relatively high concentration of OH in the atmosphere during the day, the reaction between DMSe and OH may dominate the atmospheric selenium transformation process during the daytime^[19,45]. While OH and O₃ dominate daytime Se oxidation, NO₃ and Cl may play critical roles at night and in marine boundary layers. Additionally, the potential photolysis of DMDSe (CH₃SeSeCH₃) in the troposphere, due to weaker Se–Se bonds compared to S–S bonds, warrants further investigation as it could represent an alternative degradation pathway for DMDSe^[42,45]. These future experimental studies may highlight key advances in Se oxidation mechanisms while identifying critical gaps in NO₃/Cl chemistry.

During the daytime, a series of photochemical reactions occur in the atmosphere under sunlight, generating a large number of OH radicals^[42]. These OH radicals can react rapidly with DMSe, and the reaction process involves steps such as hydrogen atom abstraction and electron transfer^[42].

The adsorption of gaseous SeO₂ onto atmospheric aerosols represents a key pathway for selenium deposition. Experimental and modeling studies show that SeO₂ exhibits strong affinity for both mineral dust (e.g., Al₂O₃, Fe₂O₃) and sulfate aerosols, with partitioning coefficients increasing significantly at elevated relative humidity due to surface hydration effects^[35]. While this adsorption enhances local deposition of Se(IV), it simultaneously limits the long-range transport of gaseous selenium. Notably, in the presence of acidic aerosols (pH < 4), adsorbed Se(IV) can be further oxidized to Se(VI), which exhibits different solubility and bioavailability patterns^[20]. These processes create complex spatial gradients in selenium deposition, with implications for both atmospheric chemistry and ecological selenium cycling. The efficiency of this conversion depends on aerosol composition, atmospheric acidity, and meteorological conditions, requiring further constraints for global models.

The oxidation products generated by the reaction of DMSe and DMDSe with oxidants such as O₃ and OH, including DMSeO and MSeA, possess certain chemical reactivity and physical properties, making them prone to adsorption onto the surface of aerosols^[19]. Aerosols, as a collection of solid and liquid particles in the atmosphere, provide a carrier for these oxidation products^[45]. During the gas-particle conversion process, the oxidation products combine with aerosols through physical or chemical adsorption, gradually forming secondary organic aerosols (SOA)^[24].

The formed SOA is transported in the atmosphere by atmospheric circulation and eventually removed through wet deposition^[18]. During wet deposition, aerosol particles containing SOA fall to the ground with precipitation such as rain or snow, thereby transferring selenium from the atmosphere to the Earth’s surface^[21]. In this process, factors such as the intensity and duration of precipitation, as well as the properties of aerosols, will affect the efficiency of gas-particle conversion and the final deposition effect^[19,29]. For instance, during heavy rainfall, many aerosol particles are rapidly washed to the ground, accelerating selenium deposition; particle size and aerosol surface properties also affect their atmospheric transport distance and the probability of being captured by precipitation^[18].

DMSe has a short atmospheric lifetime of approximately 7.6 h, primarily due to its rapid reactions with O₃ and OH^[41]. This short lifetime limits its atmospheric transport distance, hindering long-range transport^[19,32]. Under the influence of atmospheric circulation, DMSe may undergo chemical reactions and transform into other substances or return to the surface through the deposition process within a short period^[19,32].

In contrast, the reaction rate of DMDSe is relatively slow, which makes its lifetime in the atmosphere relatively long, approximately 22 h^[42]. This longer lifetime provides the possibility for regional transport of DMDSe^[42]. During atmospheric transport, DMDSe may react with other substances and be transformed into oxidation products such as MSeA^[19,32]. These oxidation products also have certain volatility and chemical reactivity, and they may continue to be transported with the atmospheric circulation, participating in the regional-scale selenium cycle^[19,32].

Weather systems, particularly thunderstorms, significantly influence the vertical transport and deposition flux of selenium^[32]. During thunderstorms, intense convection forms strong updrafts and downdrafts. The updrafts can transport selenium-containing aerosols and gases near the ground to high altitudes, changing the distribution of selenium in the atmosphere, while the downdrafts can rapidly bring selenium compounds from high altitudes to the ground, increasing the flux of selenium deposition^[18,32]. Additionally, the lightning activity accompanying thunderstorms may also affect the transformation and transport of selenium^[36]. Lightning generates high-temperature and high-pressure environments, promoting certain chemical reactions, which may alter the form and properties of selenium compounds, thereby affecting their transport and deposition in the atmosphere^[36].

Global selenium deposition is dominated by wet processes, accounting for ~80% of total fluxes, with dry deposition contributing the remaining 20%^[20]. The speciation of deposited Se is strongly pH-dependent: under acidic conditions (pH < 5), Se(IV) (SeO₃^2-) dominates due to its higher stability, whereas in neutral to alkaline environments (pH > 6), Se(VI) (SeO₄^2-) becomes the predominant form due to enhanced oxidation kinetics^[19]. This pH-mediated speciation critically influences Se bioavailability, as Se(VI) is more soluble and mobile in ecosystems. Model simulations indicate that regions with high anthropogenic emissions (e.g., industrial areas) exhibit elevated Se(IV) deposition, while marine and remote continental sites show higher Se(VI) fractions^[20]. These findings highlight the need for pH-resolved deposition schemes in global Se cycling models to accurately assess ecological impacts^[19].

Wet deposition is the main way of selenium deposition, accounting for approximately 80% of the total selenium deposition^[19,20]. During wet deposition, selenium compounds in the atmosphere are carried to the ground with precipitation (e.g., rain, snow, fog)^[46]. The pH of precipitation significantly affects the form and deposition process of selenium. Studies have shown that Se⁴⁺ is more stable under acidic conditions^[19,20]. In acidic precipitation, Se⁴⁺ may exist in a relatively stable form and be deposited on the ground with the precipitation, while in alkaline precipitation, Se⁴⁺ may undergo chemical reactions and transform into other forms, such as Se^6+[19,20]. Moreover, the chemical composition of precipitation (e.g., the presence of other ions, acidic substances) can also affect the deposition efficiency and form of selenium^[32]. Dry deposition is another way of selenium deposition, mainly referring to the process where aerosol selenium reaches the ground through gravitational settling or diffusion^[19,20]. The rate of dry deposition is influenced by various factors, including the particle size, density, and shape of aerosols, as well as the properties of the ground (e.g., roughness and vegetation coverage)^[29].

Recent SOCOL-AERv2 model simulations project significant shifts in global Se deposition patterns under a +2 °C warming scenario^[32]. The model predicts a 10%-20% increase in wet deposition fluxes at high latitudes due to enhanced precipitation, while arid regions may experience reduced removal efficiency. Altered atmospheric circulation is expected to modify long-range transport, increasing Se deposition in some oceanic regions but decreasing continental inputs. The simulations highlight climate-sensitive processes, including changing oxidant levels (OH, O₃) and aerosol chemistry, which may perturb Se speciation (Se⁴⁺/Se⁶⁺ ratios)^[32]. These projections underscore the need for coupled climate-chemistry models to assess future selenium bioavailability in ecosystems.

Online detection techniques, particularly PTR-ToF-MS and ICP-MS, play crucial roles in studying atmospheric gaseous selenium compounds^[47,48]. PTR-ToF-MS is an advanced analytical instrument capable of real-time monitoring of gaseous selenium compounds^[32,42]. It operates based on proton transfer reactions, using hydronium ions (H₃O⁺) as reagent ions. When sample gas containing target analytes (e.g., DMSe, DMDSe) enters the reaction zone, H₃O⁺ protonates them. These ions then enter the time-of-flight mass spectrometer, where they are analyzed and detected based on differences in flight time^[47,49]. Because ions of different masses follow different trajectories in electric and magnetic fields and thus have different flight times, precisely measuring ion flight time determines the mass-to-charge ratio (m/z), enabling qualitative and quantitative analysis of gaseous selenium compounds^[42,49].

PTR-ToF-MS offers significant advantages, including extremely high sensitivity for trace-level detection of gaseous selenium compounds^[42,49]. For example, in the marine boundary layer, the concentration of DMSe is usually at an extremely low level, and PTR-ToF-MS can accurately capture its concentration changes^[42,49]. In addition, it has excellent time resolution and can reflect the dynamic changes in gaseous selenium compound concentrations in real time^[41,49]. When studying the short-term fluctuations of selenium compounds in the atmosphere, such as the concentration changes affected by specific meteorological conditions or local sources, this real-time monitoring capability provides valuable data support for researchers^[42,49]. During thunderstorm observations, PTR-ToF-MS can respond quickly and present the changing trends of DMSe and DMDSe concentrations in real time, helping researchers analyze the instantaneous impact of thunderstorms on the concentrations of gaseous selenium compounds^[42,49]. PTR-ToF-MS offers exceptional sensitivity for real-time detection of volatile selenium compounds like DMSe, with typical limits of detection (LOD) ranging from 1 to 5 pptv^[42,49]. This technique provides high temporal resolution and enables continuous monitoring of dynamic atmospheric processes involving organic Se species. However, PTR-ToF-MS is limited to volatile and semi-volatile compounds and cannot detect non-volatile Se forms such as particulate-bound selenium or inorganic species like SeO₂^[42,49].

ICP-MS plays a significant role in the quantitative analysis of selenium in aerosols^[47,48]. The core principle of this technique is to ionize elements in the sample, and the resulting ion beam is separated and detected in the mass spectrometer based on the mass-to-charge ratio. When analyzing selenium in aerosols, the first step is to collect aerosol samples. Usually, devices such as filters are used to collect aerosol particles in the atmosphere, and then the collected samples are pre-treated^[47,48]. The pre-treatment process may include digestion, dissolution, and other steps, aiming to convert selenium in the aerosols into an ionizable form^[48]. The treated sample is then introduced into the ICP-MS instrument, where the selenium atoms are ionized in a high-temperature plasma environment^[47,48]. The mass spectrometer separates and detects these ions under the influence of electric and magnetic fields based on their mass-to-charge ratios. By comparison with standard samples of known concentrations, the selenium content in the aerosols can be accurately determined^[47,48]. ICP-MS has the advantages of low detection limits, fast analysis speed, and the ability to simultaneously determine multiple elements^[47,48]. Its detection limit can be as low as nanograms per cubic meter or lower, meeting the requirements for precise determination of selenium content in atmospheric aerosols. In terms of analysis speed, ICP-MS can analyze a large number of samples in a short time, improving research efficiency^[47,48]. Moreover, it can simultaneously detect multiple elements in aerosols, not only determining selenium content but also providing information on other related elements, which is helpful for studying the interrelationship between selenium and other elements as well as their synergistic effects in atmospheric processes^[47,48]. When studying atmospheric pollution in industrial areas, ICP-MS can simultaneously analyze multiple elements such as selenium, sulfur, and nitrogen in aerosols, helping researchers understand the mutual influence and transport patterns of these elements in atmospheric pollution^[19,24,47]. ICP-MS achieves ultra-low LODs (0.1-1 pg·m^-3) for total selenium in aerosols, making it ideal for quantifying trace-level particulate Se^[19,24,47]. While ICP-MS provides excellent sensitivity and multi-element capability, it requires offline filter sampling and laboratory analysis, which limits temporal resolution. Additionally, ICP-MS cannot distinguish between different Se species [e.g., Se(IV) vs. Se(VI)] or organic Se compounds without coupling with chromatography^[19,24,47]. Thus, while PTR-ToF-MS excels in real-time organic Se detection, ICP-MS remains the gold standard for total Se quantification in aerosols^[19,24,47]. The two techniques complement each other and provide a more complete understanding of atmospheric selenium cycling. In a typical field campaign, PTR-ToF-MS can be deployed for continuous, real-time monitoring of volatile organic selenium species (DMSe, DMDSe, and their oxidation products), capturing diurnal variability and pulse emissions during meteorological events such as thunderstorms^[42,47]. Simultaneously, 24-h integrated filter samples can be collected for offline ICP-MS analysis to quantify total aerosol selenium concentrations, including particulate-bound Se(IV) and Se(VI) species. By combining real-time gas-phase data from PTR-ToF-MS with time-integrated aerosol-phase data from ICP-MS, researchers can construct a more complete atmospheric selenium budget that accounts for both volatile and particulate fractions. This synergistic approach enables closure of the selenium mass balance, allowing quantification of gas-to-particle conversion rates and assessment of deposition fluxes^[19,24]. Such integrated measurements are essential for validating atmospheric chemistry models and improving our understanding of selenium’s atmospheric fate.

While the reactions of O₃ and OH with gaseous selenium compounds have been studied, the contributions of other atmospheric oxidants, such as NO₃^[50,51] and chlorine atoms (Cl)^[52,53], remain poorly quantified. Kinetic modeling and computational approaches have been instrumental in elucidating detailed reaction mechanisms between volatile selenium compounds and atmospheric radicals (OH, Cl, NO₃, and O₃)^[54-56]. These studies play a pivotal role in accurately identifying reaction pathways and characterizing the formation of both primary and secondary products. Determining site-specific and overall rate coefficients is critical for calculating atmospheric lifetimes, providing insights into the environmental persistence of these species. These methods enable precise determination of site-specific rate coefficients (e.g., •OH attack at –CH₃ vs. –Se–) and secondary product yields^[15]. Such insights are critical for refining atmospheric lifetime estimates and aerosol-formation potential^[19]. Further experimental validation is needed to confirm the theoretical predictions and improve the reliability of these models^[54-56]. Given the shared redox chemistry of the chalcogen group, the reactivity of Se compounds with NO₃ and Cl can be inferred from their S analogs (e.g., DMS/DMDS). However, because Se has lower bond dissociation energies and greater polarizability, Se compounds are expected to react faster, making the direct use of S-analog kinetics a potential source of uncertainty^[54-56].

The NO₃ usually has a relatively high concentration in the atmospheric environment at night, especially in areas with severe pollution^[50,51]. It can react with gaseous selenium compounds, but the reaction rate and products are not yet fully characterized. The NO₃ reacts with gaseous selenium compounds primarily via hydrogen abstraction or addition to the Se atom, analogous to its reactions with organic sulfides^[50,51]. For example, NO₃ likely abstracts a hydrogen atom from DMSe, forming •CH₂SeCH₃ and HNO₃, or adds to the Se center, leading to intermediate adducts. These pathways are consistent with NO₃ chemistry observed in other chalcogen systems^[44]. Gas-phase electron transfer from neutral NO₃ is unlikely; instead, reactions proceed through radical mechanisms. Studies have shown that the reaction mechanism of NO₃ with some organic compounds is rather complex, involving multiple intermediate steps and various products^[50,51]. For gaseous selenium compounds, NO₃ may change their chemical structure and properties through electron transfer or addition reactions with selenium atoms. Future research should combine laboratory simulations and field observations to elucidate the kinetics and mechanisms of NO₃ reactions with DMSe and DMDSe, and accurately quantify their contribution to selenium transformation^[50,51]. This will help provide a more comprehensive understanding of selenium transformation pathways in the atmosphere and improve atmospheric chemical models of selenium.

Chlorine atoms have relatively high concentrations in specific atmospheric environments, such as areas near the ocean or regions with industrial chlorine emissions^[52,53]. Chlorine atoms are strong oxidizers and can rapidly react with various substances^[52,53]. In marine environments, Cl radical reactions may compete with hydroxyl (OH) radicals in the atmospheric degradation of organic compounds due to the high abundance of Cl derived from sea salt aerosols^[52,53]. This represents a specialized but significant oxidation pathway, particularly for sulfur and selenium species. Villanueva et al. (2009) demonstrated that Cl reactions with organic compounds (e.g., alkylfurans) proceed rapidly, often leading to distinct degradation products compared to OH-initiated pathways^[52]. Similarly, Baptista et al. (2025) highlighted the role of Cl in the atmospheric oxidation of biofuel-related esters, showing both ring-retaining and ring-opening mechanisms^[53]. Since Cl concentrations can be elevated in coastal and marine regions, its reactions with volatile selenium compounds (e.g., DMSe) may influence their atmospheric lifetimes and transformation products. This underscores the need to consider Cl-driven chemistry alongside OH reactions when modeling marine atmospheric processes. In reactions with gaseous selenium compounds, chlorine atoms may capture electrons from selenium compounds, triggering a series of chemical reactions. However, current research on reactions between chlorine atoms and gaseous selenium compounds is relatively scarce^[52,53]. Future studies should focus on this area, employing advanced experimental techniques and analytical methods to determine the rate constants, activation energies, and reaction products, and to assess their impact on the transformation and migration of selenium in the atmosphere. It is also important to note that current global atmospheric chemistry models, such as SOCOL-AERv2 used in recent selenium deposition studies^[32,37], either completely omit NO₃ and Cl oxidation pathways for selenium species or rely on sulfur analogs (e.g., DMS and DMDS reaction rates with NO₃ and Cl) as proxies for selenium compounds. While this approach provides a first-order approximation because of chemical similarities within the chalcogen group, it introduces significant uncertainties. As discussed earlier, selenium compounds exhibit higher reactivity with oxidants than their sulfur counterparts due to weaker C–Se bonds and greater polarizability^[42,45]. Consequently, using sulfur analog kinetics may overestimate the atmospheric lifetimes of DMSe and DMDSe, particularly in regions where nocturnal NO₃ chemistry or coastal Cl chemistry is important. This oversimplification could bias predicted selenium deposition fluxes and spatial distributions. Therefore, integrating experimentally determined rate constants for Se-specific NO₃ and Cl reactions into global models represents a critical priority for improving the predictive capability of selenium biogeochemical cycling under both current and future climate scenarios.

Selenium isotope analysis is a powerful tool for studying its sources, transformation, and cycling, but the sensitivity of current techniques remains a limitation^[57-59]. Selenium has several stable isotopes, such as ⁷⁴Se, ⁷⁶Se, ⁷⁷Se, ⁷⁸Se, ⁸⁰Se, and ⁸²Se, which undergo fractionation in various geological and biological processes^[56-58]. By analyzing selenium isotope composition, the source of selenium can be traced, and the transformation processes of selenium in different environmental media can be understood^[57-59].

However, due to the low concentration of selenium in the atmosphere, existing selenium isotope analysis techniques have certain limitations in terms of sensitivity, making it difficult to accurately measure the isotope composition of trace selenium^[57-59]. In the future, it is necessary to develop high-sensitivity selenium isotope analysis techniques, such as improving the detection methods of mass spectrometers to enhance their detection capabilities for trace selenium isotopes or exploring new analytical principles and technologies, such as selenium isotope analysis methods based on laser spectroscopy, to achieve accurate measurement of trace selenium isotopes in the atmosphere. This will provide more powerful technical support for in-depth research on the biogeochemical cycle of selenium.

The impact of climate change on atmospheric selenium cycling is a complex and important topic requiring further investigation^[60]. Climate change will lead to a series of environmental changes, such as rising temperatures, altered precipitation patterns, and an increase in extreme weather events, all of which will affect the selenium cycle^[22]. Rising temperatures may affect the metabolic activities of marine and terrestrial organisms, thereby changing biogenic selenium emissions^[17,38]. A 2 °C increase may enhance biogenic Se emissions by 10%-20% due to accelerated microbial activity in wetlands and oceans^[17,32]. In the ocean, increased water temperature may affect phytoplankton growth and metabolism, altering their ability to methylate inorganic selenium and thus influencing DMSe and DMDSe emissions^[27]. Changes in precipitation patterns, such as variations in intensity and frequency, will affect selenium sedimentation^[18,22]. Increased rainfall intensity could elevate wet deposition fluxes by 15%-30% in temperate regions, while arid areas may experience reduced deposition^[18,20]. More frequent intense precipitation events may increase the wet deposition flux of selenium, but changes in the chemical composition of precipitation may also affect the form and sedimentation efficiency of selenium in precipitation^[18]. The impacts of extreme weather events, such as thunderstorms and hurricanes, on the selenium cycle also cannot be ignored^[17,37]. Thunderstorms may amplify vertical transport, increasing local deposition fluxes by up to 40% during events^[32]. Model simulations suggest net increases in Se deposition at high latitudes but declines in subtropical zones under warming scenarios^[32]. Strong convective activity in thunderstorms can rapidly transport selenium compounds to the ground, increasing selenium deposition flux, while large-scale storms like hurricanes may alter atmospheric circulation patterns, affecting selenium transport pathways and distribution^[27].

Quantitative assessments based on recent climate model projections provide initial estimates of how altered selenium deposition under warming and extreme precipitation may cascade through ecosystems. Under a +2 °C warming scenario, SOCOL-AERv2 model simulations project a 10%-20% increase in wet deposition fluxes at high latitudes due to enhanced precipitation, while arid regions may experience reduced removal efficiency^[32]. These shifts in deposition translate into differential selenium inputs to terrestrial and marine food webs. For terrestrial ecosystems, model-based estimates project a 15%-30% increase in Se deposition in northern temperate regions by 2100 under RCP8.5. This could elevate soil Se(VI) by 0.05-0.15 mg·kg^-1, potentially alleviating deficiency in agricultural soils currently below the 0.2 mg·kg^-1 threshold for plant health^[20,32]. However, in regions where increased deposition raises soil selenium concentrations above the 2 to 5 mg·kg^-1 toxicity threshold, especially in historically seleniferous areas, soil microbial communities may suffer from reduced diversity and activity. This occurs because selenate competes with sulfate for microbial uptake, thereby disrupting normal sulfur metabolism^[33]. For small fauna (e.g., soil invertebrates and herbivorous mammals), a 0.1-0.3 mg·kg^-1 increase in dietary Se intake could elevate tissue Se concentrations by 1.5-2.5-fold, potentially leading to chronic selenosis symptoms including reproductive impairment and growth inhibition^[16]. In regions with reduced precipitation, such as Mediterranean and subtropical zones where deposition is projected to decline by 10 to 20 percent, soil selenium levels may fall by 0.05 to 0.1 mg·kg^-1. This decline exacerbates selenium deficiency and has cascading effects on livestock health, because dietary selenium below 0.05 mg·kg^-1 is associated with increased incidence of white muscle disease and immune dysfunction^[3].

For marine ecosystems, the impacts are more nuanced due to the long residence time of Se in the ocean. Model outputs suggest that climate-driven changes in ocean circulation and stratification may alter vertical Se transport, with potential 5%-15% reductions in phytoplankton-available Se(VI) in the euphotic zone under warming scenarios^[2,12]. This could translate into a 10%-20% decrease in DMSe emissions from marine biogenic sources, as Se uptake by phytoplankton is directly linked to primary productivity^[8]. Conversely, increased extreme precipitation events (projected 20%-30% increase in frequency in tropical regions) may enhance riverine Se inputs to coastal waters by 15%-25%, potentially shifting the Se(IV)/Se(VI) ratio in estuarine environments and affecting selenium bioavailability for marine microorganisms^[18,20]. The net effect on marine food webs from phytoplankton to higher trophic levels remains uncertain and warrants integrated modeling approaches that couple atmospheric chemistry, ocean biogeochemistry, and ecosystem response functions. These quantitative projections underscore the need to refine climate-chemistry-ecology coupled models to better constrain the cascading ecological consequences of climate-driven alterations in selenium deposition and speciation. Future work should combine climate models, atmospheric chemistry models, and long-term observations to assess climate change impacts on the selenium cycle.