Reaction rate constant for O3 and OH reacting with inorganic compounds.
Abstract
Electrical pulsed discharge plasma produces various powerful oxidizing agents, such as hydroxyl radicals and ozone, which have high oxidation potential. These species play an important role in the decomposition of persistent organic compounds in wastewater. Because highly concentrated oxidants are directly produced inside the plasma, plasma realizes high-speed wastewater treatment without pretreatment of samples, such as pH adjustment. The pulsed discharge plasma generated over the water surface and inside bubbles is highlighted as a highly efficient method for plasma generation and radical supply into wastewater. In this paper, the physical and chemical properties of the discharge plasma generated over a water surface are described. The decomposition of persistent organic compounds dissolved in wastewater, such as 1,4-dioxane, formic acid, and dichloromethane, by plasma discharge is demonstrated, and their mechanisms are discussed. These persistent compounds, which have strong toxicity and stability, can be efficiently decomposed and removed quickly from solutions by plasma treatment. Furthermore, the treatment of nutrient solutions used in hydroponic systems for plant cultivation is also introduced as a novel application of plasma, and the effects of bacterial inactivation, decomposition of allelochemicals, and improvement in plant growth by plasma are demonstrated.
Keywords
- plasma
- wastewater
- persistent compounds
- advanced oxidation process
- hydroxyl radical
- oxidation
- ozone
1. Introduction
Electrical pulsed discharge under water, an advanced oxidation process (AOP), can instantaneously produce chemically active species such as hydroxyl radicals and ozone in a nonthermal plasma [1, 2, 3]. It is well known that these species are powerful oxidizing agents that play an important role in degrading persistent organic chemical compounds and sterilizing bacteria in wastewater [4, 5]. Hydroxyl radicals can contribute to the decomposition of persistent organic pollutants, which cannot be decomposed by conventional methods because of their very high oxidation potential. Wastewater treatment using discharge plasma has several advantages over other AOPs. In the plasma system, active species are directly produced in plasma through various reactions initiated by high-energy electron impact. These active species are directly dissolved into water, and then oxidation reactions are induced. Because only electricity-supplied metal electrodes and a high voltage power supply are needed to generate plasma, pretreatment of water, such as pH adjustment is not required for active species production, unlike other AOPs such as Fenton and ozone/hydrogen peroxide methods [6]. Plasma can also be adapted for the treatment of water, which has ultraviolet (UV) light non-transmitting properties, which is advantageous over AOPs utilizing UV light, such as photocatalytic processes and UV-hydrogen peroxide methods. In the case of plasma discharge in contact with water, the types of active species produced in plasma can vary by atmospheric gas species. The production of active species can be localized near the plasma channel. Thus, water treatment using plasma discharge can be useful in various uses. Furthermore, because the density of active species in plasma is very high, it can also be used for the treatment of highly concentrated wastewater. These characteristics of discharge plasma can make the system simple, easy to use and easy to install anywhere. Owing to these advantages, the plasma technique has attracted attention as a promising method in various fields, such as industrial and environmental wastewater treatment [4, 6, 7] and material [8], agricultural [9, 10], and medical applications [11].
In this article, characteristics of discharge plasma generated by pulsed high voltages, chemical reactions induced by plasma, and treatment of persistent organic pollutants such as 1,4-dioxane and dichloromethane dissolved in water by plasma discharges are introduced. Agricultural applications of discharge plasma in contact with water surfaces are also mentioned as a novel application.
2. Generation of pulsed discharge plasma
Plasma is one of the states of matter and consists of high-density electrons and ions produced through ionization reactions of neutral gas atoms and molecules. Ionization is initiated by an impact of high-energy electrons accelerated by a high electric field; then, the electron and ion densities rapidly increase due to an electron avalanche phenomenon, and plasma forms [12]. To generate a high electric field, a sharpened metal electrode to which a high voltage is applied is generally used. Although various kinds of voltage waveforms, such as DC and AC, are employed, a pulsed high voltage generated by a pulsed power generator is used for highly efficient plasma generation, [13, 14] especially under water. Pulsed power is a special technology used to generate a pulse voltage that has a high voltage amplitude over several tens of kV, high power over several tens of kW, short pulses on the order of nanoseconds, and high pulse frequencies over several kHz, achieved with a compact system [15].
When a pulsed high voltage is applied to pointed electrodes immersed in water, discharge plasma is generated at the tip of the electrode. One of the formation mechanisms of the discharge plasma in water using a long pulse voltage on the order of several μs is considered as follows: In the first step, the discharge is initiated in a small bubble on the electrode surface, and then it propagates into the water, as shown in Figure 1. The current in the high electric field region causes Joule heating and vaporization of the liquid, forming bubbles [16, 17, 18]. The electron density in the plasma directly generated under water is very high, on the order of 1025 m−3 [19], which can produce very high density chemically active species such as hydroxyl radicals and contribute to high-speed wastewater treatment. The plasma discharge under water can also produce strong shock waves with pressure on the order of several GPa. The problem with this method is that wastewaters exhibit high conductivity due to the high concentration of various substances. When a voltage is applied to the electrodes immersed in water, which has high conductivity, a large current flow, and large energy are dissipated during Joule heating, which does not contribute to chemically active species production. The discharge volume decreases with increasing conductivity of the water at the same input energy. As a result, the energy efficiency for water treatment by discharge decreases to a low value under high-conductivity water conditions. Furthermore, because the breakdown strength of water is 300 MV/m and is 10 times higher than that of air (3.2 MV/m), high voltage is required to generate plasma discharges under water and to increase plasma volume. To solve this problem, methods to generate a pulsed discharge in contact with water using an electrode in the gas phase have been investigated [20, 21, 22]. Because the electrode is insulated by gas, the energy loss caused by the conductive current is significantly reduced. Plasma generation in the gas phase is much easier than that in the liquid phase, which contributes to a decrease in operating voltage and makes the system compact and light.
Various methods to generate a pulsed discharge in contact with water have been proposed [23, 24]. Figure 2 shows schematic illustrations and photographs of examples. The simplest method is to generate discharge that propagates and spreads over the water surface by using a high-voltage electrode placed above stationary water, [25, 26] as shown in Figure 2(a). The chemical species generated in the plasma discharge are dissolved into the water and react with organic compounds in the water as described later. The discharges generated inside bubbles as shown in Figure 2(b), which are produced by injecting gas into the water using a gas feed tube, have been widely investigated [23, 26, 27, 28]. This method has advantages such as a high ratio of water surface to gas volume, easy control of the gas purity and components, easy use in various fields, and automatic water circulation. The reactor can be simply constructed as shown in Figure 3(a) [29]. This reactor consists of a sealed glass vial for gas chromatography and glass tubes in which wire electrodes are inserted. Because the glass vial is sealed, the purity of the gas component in the reaction area in the vial can be improved. The treatment speed and volume can be increased easily by increasing the number of gas feed tubes and electrodes, as shown in Figure 3(b). Figure 3(c) shows a reactor consisting of a separator film that has tiny pores and a high voltage wire electrode in the gas phase [20]. Multiple discharge plasmas occur simultaneously on the wire electrode surface, which propagates into the bubbles. The separator film is used to separate the liquid phase and gas phase for insulation of the high voltage electrode. Instead of the separator and the wire electrode, ceramics with millipore needle electrodes have been used in some studies [7, 30].
When a pulsed high voltage is applied to the high-voltage electrode in the gas phase, the discharge propagates into the bubble surface from the high-voltage electrode [31, 32]. Figure 4 shows typical voltage–current waveforms and flaming photographs of the pulsed discharge generated in an argon bubble, as shown in Figure 2(b) taken by using an intensified CCD camera with an exposure time of 5 ns. At time
Conductivity is the most important parameter for discharge propagation. Generally, the energy efficiency for discharge generation and propagation over a water surface is strongly affected by the conductivity of the water [32, 37]. Figure 5 shows the equivalent circuit model [38] of (a) discharge in contact with water using the electrode system shown in Figure 2(b) discharge generated under water using the electrode system shown in Figure 1. When a breakdown occurs, switch SW1 is turned on. The plasma impedance
When the electrode is placed in the gas phase and is not in contact with water, conductive current does not flow into the water without plasma generation,
To reduce the influence of the conductivity, a method to generate streamer discharges into the area where droplets are sprayed using a pulsed high voltage is proposed as shown in Figure 2(b) [40]. This is one of the most efficient methods to supply chemical species into the water because streamer generation in the gas phase is not affected by water droplets, and the contact area between the discharge and water is large.
3. Production of chemical species by discharge plasma
In the plasma generated in the gas phase, various chemically active species such as ozone (O3), oxygen radicals (O), and hydroxyl radicals (OH) are produced and dissolved at the water surface. Since these species have a high oxidation potential, they can contribute to wastewater treatment,
where (3) is a three-body recombination reaction and a neutral molecule such as O2, N2 or Ar is the third collision partner (M), which takes part in energy absorption, but does not react chemically. Ar, a noble gas, is generally used for highly efficient plasma generation at low cost. Because the reaction rates of (11) and (12) are not high in atmospheric nonthermal plasma, OH is mainly produced by indirect reactions such as reactions (4), (6) and (10) [44, 45, 46]. When a water surface is used as the cathode, OH is also produced under water by the bombardment of high-energy positive ions produced inside plasma, such as H2O+ and Ar+, to the water surface [47, 48].
Figure 6 shows typical emission spectra of the discharge inside the Ar or O2 bubble. The peaks at wavelengths of 282 and 308 nm are the A2Σ+ (
Because these oxidants have high reactivities, they are consumed in loss reactions in both the gas and aqueous phases, which decreases the efficiency of wastewater treatment as shown in Figure 8. OH is well known as the most powerful oxidant and has a very short lifetime. OH is mainly lost by three-body recombination reactions, as shown in reaction (17) in the gas phase and reactions (18) and (19) in the aqueous phase [49, 50].
The lifetime and diffusion constant of OH in the gas phase are on the order of 10−5 s and 10−10 m2/s, respectively, and the diffusion length is several tens of μm [51]. The lifetime of dissolved OH is on the order of 10−6 ∼ 10−7 s with penetration lengths on the order of 10−5 ∼ 10−6 m [52, 53, 54]. Figure 9 shows the hydrogen peroxide (H2O2) concentration produced by the OH recombination reaction, as described later, as a function of treatment time by plasma generated inside Ar or O2 bubbles. In this case, 100 mL of dye solution was treated by plasma discharges generated inside bubbles produced by multiple pores, as shown in Figure 3(c). The gas flow rate is 4.5 L/min. Pulse voltages with an amplitude of 20 kV, a pulse width of 160 ns, and a pulse repetition rate of 250 Hz are applied to the wire electrode placed in the gas phase to generate plasma [73]. The electric power into the plasma is the same in both gas species at 3.4 W. H2O2 concentration,
Many researchers have analyzed the amount of dissolved OH in water using chemical probes such as terephthalic acid [55, 56]. The energy yield for the surface pulsed streamer discharge on the liquid with argon gas is estimated to be 13 ∼ 27 × 10−9 mol/J with disodium terephthalate solution [57]. The typical energy yield of dissolved OH in water supplied by plasma, which can react with solutes in water, is estimated to be 4 ∼ 5 × 10−9 mol/J using the indigo carmine solution as a chemical probe [29]. Because plasma directly generated under water has a high OH density, the reaction rate of OH loss reactions is very high, which decreases the energy efficiency for OH supply.
When the feeding gas contains O2, highly concentrated O3 is generated in the plasma through reactions (1) ∼ (3). Henry’s law constants for O3 and OH are 0.011 and 30 M/atm at 298 K, [58] respectively, which shows that the solubility of O3 is lower than that of OH. Additionally, the oxidation potential of O3 is lower than that of OH. However, the lifetime of O3 in water is on the order of several min [59, 60, 61] and much longer than that of OH. Thus, when wastewater contains only organic compounds that can be easily oxidized by O3, the treatment efficiency utilizing O3 is higher than that utilizing OH. In this case, O2 is preferred for use as a feeding gas for high-efficient O3 production. O3 dissolved in water can contribute to OH production via the following reaction with hydroperoxide anion (HO2−) species, the conjugate base of H2O2, under alkaline conditions with a high reaction rate [62].
The pKa value of the equilibrium reaction (R14) is 11.6. Because the reaction rate of O3 and H2O2 is very low (10−2 M−1 s−1), O3 mainly reacts with HO2− with a reaction rate constant of 5.5 × 106 M−1 s−1 and hardly reacts with H2O2 directly. Thus, pH adjustment is required to induce this OH production reaction.
When the feeding gas contains nitrogen, nitrous (HNO2) and nitrite (HNO3) acids, are generated by plasma as byproducts through the following reactions; [46, 63, 64, 65].
Peroxynitric acid (HOONO2) contributes to HOO production via equilibrium decomposition reaction, [66].
When HNO2 and HNO3 are dissolved in water, nitric and nitrate ions are easily produced in water through acid dissociations of HNO2 and HNO3 because of their low pKa values, of 3.35 and − 1.8, respectively, and the pH of the solution significantly decreases [65, 67].
NO2− is oxidized to NO3− by O3 in solution [68]. When the pH is lower than 3.5, NO2− is oxidized by H+. These reactions are follows:
These nitrogen species can contribute to the inactivation of bacteria in wastewater as described later. In the case of plasma discharges inside multiple air bubbles using a reactor similar to that in Figure 3(b) with eight glass tubes in which total air gas with a flow rate of 5 L/min is injected, approximately 9 mM NO3− is generated in 20 L of solution with 24 hours of plasma treatment, [69] which is a sufficient concentration for using fertilizers in plant cultivation. This effect is described in Section 5.
When metals that are easily oxidized by electrolysis, such as iron and copper, are used as an electrode immersed in water, metal ions such as Fe2+, Fe3+, Cu+, and Cu2+ are generated by electrooxidation by a large discharge current, and the metal ion concentration increases. These metal ions contribute to the oxidation of organic compounds in wastewater not only directly but also through OH production by redox reactions well known as Fenton reactions with H2O2 produced by plasma as follows: [70, 71, 72, 73].
Reactions related to iron ions are well known as Fenton reactions and occur under acidic conditions. Generally, electrodes immersed in water are used as grounded electrodes to keep the voltage potential of water zero for safety reasons. Therefore, when a positive (or negative) high voltage is applied to a high voltage electrode, iron (or copper) ions are dissolved from the grounded electrode immersed in water and used as the anode (or cathode). For example, in the case of 1,4-decomposition as described in Section 4, the decomposition efficiency can be improved by approximately three times, by using iron wire as an electrode immersed in water, compared with that achieved using stainless steel wire [73].
The chemical species dissolved in the water react with not only organic compounds but also inorganic compounds. Table 1 shows reaction the rate constants for O3 and OH reacting with inorganic ions [74, 75, 76, 77, 78]. Halogen ions such as chloride ions (Cl−), bromide ions (Br−) and iodide ions (I−) have high reactivity toward O3 and OH and act as O3 and OH scavengers, which inhibits the decomposition reactions of organic compounds. Furthermore, toxic compounds such as hypochlorite ions (ClO−) and bromate ions (BrO3−) are produced via oxidation reactions, as shown in Figures 10 and 11. Carbon dioxide radicals (CO2−), carbonate radicals (CO3−), and sulfate radicals (SO4−) are produced through reactions of OH with formate ions (HCO2−), carbonate ions (CO32−), and hydrogen sulfate ions (HSO4−) with hydroxyl radicals in liquid [79]. These radicals also contribute to the decomposition of organic compounds dissolved in wastewater as synergistic effects. Although hydroxide ions (OH−) and per hydroxyl ions (HO2−) act as scavengers of OH, OH can be produced via reaction with O3 under high-pH conditions. Thus, the influence of these ions on treatment efficiency and water quality after wastewater treatment using plasma should be considered.
Solute | Reaction rate constant for O3 [M−1 s−1] | Reaction rate constant for OH [M−1 s−1] |
---|---|---|
Cl− | 0.003 | 4.3 × 109 |
Br− | 160 | 1.1 × 109 |
I− | 1.2 × 105 | 1.1 × 1010 |
NO2− | 3.7 × 105 | 1.0 × 1010 |
NO3− | — | 1.0 × 105 |
HSO3− | 3.7 × 105 | 4.5 × 109 |
SO32− | 1.5 × 109 | 5.1 × 109 |
HSO4− | <10−4 | 6.9 × 105 |
H2SO4 | — | 1.4 × 107 |
H2O2 | 0.01 | 2.7 × 107 |
HO2− | 5.5 × 106 | 7.5 × 109 |
HCO3− | 0.01 | 8.5 × 106 |
HCO2− | 100 | 5.1 × 109 |
CO32− | 0.01 | 3.9 × 108 |
CO2 | — | 1 × 106 |
OH− | 210 | 1.2 × 1010 |
4. Decomposition of persistent organic pollutants
Organic pollutants entering the water environment cause industrial, agricultural, domestic, livestock, and medical wastewater drainage into and leakage from polluted soil. Because most organic pollutants have strong toxicity, carcinogenicity, and genotoxicity, even at low concentrations, it is urgent to develop effective technologies for the highly efficient removal of these contaminants from water. 1,4-Dioxane has been widely used as a solvent. Because it has high solubility and is hard to absorb to the bottom material, it can be widely spread in water environments [80, 81]. Dichloromethane (DCM) is a chlorinated volatile organic compound (Cl-VOC) and has high volatility. It is also used as a solvent, cleaner, degreasing agent, and liquid fuel and released into the environment through water discharge from chemical industries [82, 83]. These compounds are very difficult to decompose using conventional oxidation treatment methods such as chlorine, ozone oxidation, and bioremediation owing to their chemical and biological stability.
In wastewater treatment systems using plasma discharges, high-density powerful oxidants such as OH and O3 produced by plasma contribute to the decomposition of persistent organic pollutants and the inactivation of bacteria. This method provides high-speed treatment and decomposition of organic compounds that are difficult to remove with conventional methods and has attracted much attention as an advanced oxidation technology. Many researchers have proposed that plasma treatment is effective for the decomposition of various kinds of toxic aromatic hydrocarbons, such as chlorophenol, [84] naphthalene, toluene [85], and bisphenol A [86], and volatile organic compounds such as trichloroacetic acid [87]. Oxidants also contribute to the quick decolorization of wastewater containing dye solutions [88, 89]. In this section, the decomposition of various kinds of organic compounds in water is systematically described. The decomposition characteristics of indigo carmine, a common blue dye, 1,4-dioxane [73] which has a high solubility in water, and formic acid, [90] which is an intermediate product of various organic compounds, such as dichloromethane (DCM), [91] which is a volatile organic compound, are introduced as an example.
Chemically active species dissolve in water in the vicinity of the water surface and induce oxidation reactions such as hydrogen atom abstraction, electron transfer, electrophilic addition, and chain oxidation reactions triggered by these reactions. The following reactions are typical oxidation reactions of organic compounds induced by OH.
Indigo carmine and azo phloxine are common dyes and have blue and red colors, respectively. Figure 12 shows the time change of appearance and UV–vis spectra of two dye solutions, (a) indigo carmine and (b) azo phloxine, by treatment using plasma generated inside O2 gas bubbles. In this case, 100 mL of dye solution was treated by plasma discharges generated inside bubbles produced by multiple pores as shown in Figure 3(c). The gas flow rate is 4.5 L/min. Pulse voltages with an amplitude of 20 kV, a pulse width of 160 ns, and a pulse repetition rate of 250 Hz are applied to the wire electrode placed in the gas phase to generate plasma [73]. The energy input into a pulse is fixed at 13.5 mJ for each gas species by adjusting the voltage amplitude. From the input energy and pulse repetition rate, the input power can be estimated as 3.4 W. Indigo carmine and azo phloxine have absorbance peaks at wavelengths of 610 nm and 531 nm, which are responsible for the blue and red colors of their solutions, respectively. These peaks decrease, the colors disappear after 20 s and 180 s of plasma treatment, and then the solutions are fully decolorized after treatment. This result shows that plasma treatment is effective for the decolorization treatment of wastewater. Figure 13 shows the decolorization rate of these solutions using Ar and O2 as feeding gases to generate bubbles. Decolorization of both solutions in the case of O2 injection is much faster than that of Ar injection. The energy efficiency for 50% decolorization of indigo carmine is 1.3 × 103 mmol/kWh for O2 injection and 6.1 mmol/kWh for Ar injection, and those of azo phloxine are 77 mmol/kWh for O2 injection and 4.8 mmol/kWh for Ar injection. The absorbance peaks of these dyes are due to the carbon–carbon double bond in the H-chromophore of indigo carmine and the nitrogen-nitrogen double bond of the azo chromophore of azo phloxine as shown in Figure 14, which are responsible for the blue and red colors of the solution. These double bonds have high electron density and high reactivity to electrophilic OH. It is well known that O3 reacts with C-C and N-N double bonds rapidly; however, the reaction of OH with dyes is at least four orders of magnitude faster than that of O3. As already mentioned, the lifetime of OH in water is much shorter than that of O3 because of its high reactivity and high rate constant of recombination loss reactions, and only OH generated in the vicinity of the bubble surface can be dissolved in the solution. In this case, these two dyes can be easily oxidized by O3. Therefore, O2 injection to generate O3 at high efficiency is preferred for the decomposition of compounds that have high reactivity to O3. The reactivity of an azo group with ozone is very low compared to that of olefins, [92] which is one of the reasons that indigo carmine is more readily decolorized than azo phroxine.
Since 1,4-dioxane has low reactivity to O3 due to its high chemical stability, plasma treatment is a promising method for 1,4-dioxane removal. Figure 15 shows one of the proposed decomposition processes of 1,4-dioxane by hydroxyl radicals [93, 94, 95]. The reaction is initiated by hydrogen atom abstraction, and various reactions, such as chain reactions, are involved. Carboxylic acids such as formic acids (HCOOH) and oxalic acid ((COOH)2) are produced as intermediate products. Figure 16 shows the time change of the TOC concentration of the 1,4-dioxane solution with an initial concentration of 0.23 mM with two different injected gases and with and without discharges. The experimental conditions were the same as those mentioned above. The electric power in the plasma is the same in both gas species. The TOC decreases without discharges because of the volatilization by bubbling gas, and the TOC concentration in the O2 injection is almost the same without discharges. The rate of TOC decrease rate in the case of Ar injection is much higher than that in the case of O2 injection. 1,4-dioxane hardly reacts with O3 because of its low reaction rate (0.32 M−1 s−1) [78]. The rate constant of reaction between OH and 1,4-dioxane is 2.4*109 M−1 s−1 [96]. The production rate of OH in the case of Ar injection is much higher than that in the case of O2 injection. Thus, Ar injection is preferred for the decomposition of organic compounds that have low reactivity to O3. The energy efficiency for 1,4-dioxane decomposition is 2 mmol/kWh.
Figure 17 shows the oxidation of acetic acid (CH3COOH) by OH radicals. CH3COOH has also low reactivity to O3. It can be decomposed into formic acid, oxalic acid, and finally, CO2 and H2O by oxidation reactions with OH. These acids have an acidity constant and are in equilibrium with their conjugated bases. For example, formic acid is in equilibrium with its conjugate base, formate, as follows:
The pKa value of this equilibrium reaction is 3.75. The reaction processes of formic acid and formate with OH and O3 are represented by the following: [76, 78].
The rate constant of reaction (62) is 100 M−1 s−1 and is 20 times higher than that of reaction (60) (5 M−1 s−1). Similarly, the rate constant of reaction (63) is 3.2 × 109 M−1 s−1 and is 25 times higher than that of reaction (61) (1.3 × 108 M−1 s−1). Therefore, decomposition of these acids at higher pH is preferred. It has been reported that the decomposition rate of formic acid can be improved twice by increasing the pH from 3.5 to 4.2 with the addition of sodium carbonate, in the case of plasma generated inside oxygen bubbles using the reactor shown in Figure 3(a) [90]. Thus, pH adjustment is an important factor for wastewater treatment, while active species can be directly supplied from plasma.
The decomposition process of DCM is different from that of other soluble compounds because of its high volatility. The rate constant of DCM reacting with OH in a liquid is 2.2 × 107 M−1S−1 [97] and is much lower than that of reactions of other soluble organic compounds, such as 1,4-dioxane, phenol, and formic acids, with OH (on the order of 109 M−1 s−1). Figure 18 shows the TOC and the amount of decomposed DCM as a function of treatment time using plasma generated inside Ar bubbles using the reaction shown in Figure 3(a). The gas flow rate is 30 mL/min. Pulse voltages with an amplitude of 16 kV, a pulse width of 160 ns, and a pulse repetition rate of 250 Hz are applied to the wire electrode placed in the gas phase to generate plasma [91]. The amount of decomposed DCM is calculated from the Cl− concentration detached from DCM during the decomposition process. The TOC decreases without discharges because of volatilization by bubbling gas. DCM can be successfully decomposed by discharges generated inside Ar bubbles [91]. The energy efficiency for DCM decomposition is approximately 60 mmol/kWh and is much higher than that for decolorization of dye solutions and 1,4-dioxane decomposition, as mentioned above, although the rate constant for DCM reacting with OH is low. This result suggests that almost all DCM is decomposed in the gas phase in the bubble, not in the liquid phase. DCM is quickly volatilized due to its high volatility and is transferred into the gas phase in the bubble when Ar gas is fed into the DCM solution, and DCM is exposed by plasma discharges generated inside the bubble. DCM can be decomposed by OH with the following reactions: [98].
The Cl-H bonding energy of CH2Cl2 is 4.28 eV and is lower than the energy of metastable Ar (11.55 eV) produced by electron impact, as shown in reaction (9) [99]. Therefore, CH2Cl2 is also possibly decomposed by Penning ionization by the energy transfer collision of metastable Ar (Ar*) as shown in the following reactions: [99, 100].
Because the concentration of DCM inside the gas bubble is on the order of several hundred ppm as mentioned previously, and is much lower than the Ar and H2O concentrations, the DCM dissociation by electron impact is negligible [98, 101].
5. Novel applications for agriculture
Agricultural applications of plasma have been widely investigated in recent years and have become one of the most attractive research topics in plasma science [102, 103, 104, 105]. As already mentioned in this article, plasma in contact with water can produce various types of chemically active species, which have various effects on the environment of plant growth.
As a production process of fruits and vegetables, hydroponics, which is the method of growing plants without soil using the nutrient solution, has been widely used. In hydroponics, the nutrient solution is recirculated in a closed system to reduce the cost and the environmental load. In the system, plant diseases caused by microbial contamination of artificial nutrient solution rapidly spread in the circulation system and cause serious damage to the entire plant. During the entire period of plant growth, contamination with pathogens can never be excluded since pathogens are introduced in the nutrient solution via the irrigation water supply. Therefore, the nutrient solution should be remedied by continuous water treatment system operation during the cultivation period. Active species such as OH and O3 produced by discharges can contribute to the inactivation of pathogenic bacteria-contaminated in liquid fertilizer. A plasma treatment system for the inactivation of
Not only radicals such as O3 and OH, but also nitrogen species such as ONOO− and O2NOOH can be key inactivation agents that cause cell damage and inactivation under acidic conditions. Because these nitrogen species have a long lifetime in the liquid phase, nitrogen species generated by plasma treatment remain for a long time after nonthermal plasma irradiation. It has been reported that nonthermal plasma-activated water (PAW), water irradiated by nonthermal plasma, can inactivate bacteria on the surface of fruits and vegetables [109] such as strawberries, [110] mushrooms [111] and endives, [112] which contributes to maintaining the freshness of fruits and vegetables.
6. Conclusion
The fundamental physical and chemical properties of plasma discharge generated over a water surface and its applications for the decomposition of persistent compounds are described. Plasma can directly generate powerful oxidizing agents such as hydroxyl radicals, which can realize high-speed decomposition of persistent compounds in wastewater, such as 1,4-dioxane and dichloromethane, without pretreatment of samples. Because of these advantages over other advanced oxidation processes, a pulsed discharge plasma in water and in contact with water has attracted much attention as a promising technology in not only wastewater treatment but also various new application fields such as agriculture.
Authors are grateful to Prof. Y. Minanitani in Yamagata University, Japan for providing a photograph of discharge used in Figure 2(c). This research was supported by a grant-in-aid from the Ministry of Agriculture, Forestry and Fisheries of Japan (A scheme to revitalize agriculture and fisheries in disaster areas through deploying highly advanced technology), by a grants-in-aid for Scientific Research (S), (A), (B), (C) and early-career scientists, from the Japan Society for the Promotion of Science, Grant Numbers 19H05611, 15H02231, 20,370,130, 21 K03994, 18 K13735 and respectively, and by Joint Usage/Research by the Institute of Pulsed Power Science, Kumamoto University.
References
- 1.
Attri P, Sarinont T, Kim M, Amano T, Koga K, Cho AE, et al. Influence of ionic liquid and ionic salt on protein against the reactive species generated using dielectric barrier discharge plasma. Scientific Reports. 2015; 5 :17781. DOI: 10.1038/srep17781 - 2.
Nakajima A, Uchida G, Kawasaki T, Koga K, Sarinont T, Amano T, et al. Effects of gas flow on oxidation reaction in liquid induced by He/O2 plasma-jet irradiation. Journal of Applied Physics. 2015; 118 :043301. DOI: 10.1063/1.4927217 - 3.
Graves DB. The emerging role of reactive oxygen and nitrogen species in redox biology and some implications for plasma applications to medicine and biology. Journal of Physics D: Applied Physics. 2012; 45 :263001. DOI: 10.1088/0022-3727/45/26/263001 - 4.
Huang Y, Kou Y, Zheng C, Xu Y, Liu Z, Yan K. Escherichia coli inactivation in water using pulsed discharge. IEEE Transactions on Plasma Science. 2016; 44 :2654-2655. DOI: 10.1109/TPS.2016.2559802 - 5.
Kirkpatrick MJ, Dodet B, Odic E. Atmospheric pressure humid argon DBD plasma for the application of sterilization- measurement and simulation of hydrogen, oxygen, and hydrogen peroxide formation. International Journal of Plasma Environmental Science and Technology. 2007; 1 :96-101 - 6.
Miklos DB, Remy C, Jekel M, Linden KG, Hübner U. Evaluation of advanced oxidation processes for water and wastewater treatment – A critical review. Water Research. 2018; 139 :118-131. DOI: 10.1016/j.watres.2018.03.042 - 7.
Takeuchi N, Yasuoka K. Review of plasma-based water treatment technologies for the decomposition of persistent organic compounds. Japanese Journal of Applied Physics. 2021; 60 :SA0801. DOI: 10.35848/1347-4065/abb75d - 8.
Qin L, Kim K, Takahashi K, Kang J, Takeuchi N, Li OL. N2/Ar plasma-induced surface sulfonation on graphene nanoplatelets for catalytic hydrolysis of cellulose to glucose. Applied Surface Science. 2021; 545 :149051. DOI: 10.1016/j.apsusc.2021.149051 - 9.
Takahashi K, Saito Y, Oikawa R, Okumura T, Takaki K, Fujio T. Development of automatically controlled corona plasma system for inactivation of pathogen in hydroponic cultivation medium of tomato. Journal of Electrostatics. 2018; 91 :61-69. DOI: 10.1016/j.elstat.2017.12.006 - 10.
Takaki K, Hayashi H, Wang D, Ohshima T. High-voltage technologies for agriculture and food processing. Journal of Physics D: Applied Physics. 2019; 52 :473001. DOI: 10.1088/1361-6463/ab2e2d - 11.
Tanaka H, Ishikawa K. State of the art in medical applications using non-thermal atmospheric pressure plasma. Reviews of Modern Plasma Physics. 2017; 1 :1-89. DOI: 10.1007/s41614-017-0004-3 - 12.
Fridman A, Chrokov A, Gutsol A. Non-thermal atmospheric pressure. Journal of Physics D: Applied Physics. 2005; 38 :R1-R24. DOI: 10.1088/0022-3727/38/2/R01 - 13.
Huiskamp T. Nanosecond pulsed streamer discharges Part I : Generation , source-plasma interaction and energy-ef fi ciency optimization. Plasma Sources Science and Technology. 2020; 29 :023002. DOI: 10.1088/1361-6595/ab53c5 - 14.
Wang D, Namihira T. Nanosecond pulsed streamer discharges : II . Physics , discharge characterization and plasma processing. Plasma Sources Science and Technology. 2020; 29 :023001. DOI: 10.1088/1361-6595/ab5bf6 - 15.
Mankowski J, Kristiansen M, Fellow L. A review of short pulse generator technology. IEEE Transactions on Plasma Science. 2000; 28 :102-108. DOI: 10.1109/27.842875 - 16.
Wetz DA, Mankowski JJ, Dickens JC, KristiansenM. The impact of field enhancements and charge injetion on the puled breakdown strength of water. IEEE Transactions on Plasma Science. 2006; 34 :1670-1679. DOI: 10.1109/TPS.2006.881891 - 17.
Gavrilov IM, Kukhta VR, Lopatin VV, Petrov PG. Dynamics of prebreakdown phenomena in a uniform field. IEEE Transactions on Dielectrics and Electrical Insulation. 1994; 1 :496-502. DOI: 10.1109/94.300293 - 18.
Clements JS, Sato M, Davis RH. Preliminary investigation of prebreakdown phenomena and chemical reactions using a pulsed high-voltage discharge in water. IEEE Transactions on Industry Applications. 1987; IA-23 :224-235. DOI: 10.1109/TIA.1987.4504897 - 19.
Bruggeman P, Leys C. Non-thermal plasmas in and in contact with liquids. Journal of Physics D: Applied Physics. 2009; 42 :053001. DOI: 10.1088/0022-3727/42/5/053001 - 20.
Takahashi K, Sasaki Y, Mukaigawa S, Takaki K, Fujiwara T, Satta N. Purification of high-conductivity water using gas–liquid phase discharge reactor. IEEE Transactions on Plasma Science. 2010; 38 :2694-2700. DOI: 0.1109/TPS.2010.2049505 - 21.
Levko D, Sharma A, Raja LL. Plasmas generated in bubbles immersed in liquids: direct current streamers versus microwave plasma. Journal of Physics D: Applied Physics. 2016; 49 :285205. DOI: 10.1088/0022-3727/49/28/285205 - 22.
Hamdan A, Cha MS. The effects of gaseous bubble composition and gap distance on the characteristics of nanosecond discharges in distilled water. Journal of Physics D: Applied Physics. 2016; 49 :245203. DOI: 10.1088/0022-3727/49/24/245203 - 23.
Bruggeman PJ, Kushner MJ, Locke BR, Gardeniers JGE, Graham WG, Graves DB, et al. Plasma–liquid interactions: a review and roadmap. Plasma Sources Science and Technology. 2016; 25 :53002. DOI: 10.1088/0963-0252/25/5/053002 - 24.
Malik MA. Water purification by plasma which reactors are most energy efficient? Plasma Chemistry and Plasma Processing. 2010; 30 :21-31. DOI: 10.1007/s11090-009-9202-2 - 25.
Kanazawa S, Kawano H, Watanabe S, Furuki T, Akamine S, Ichiki R, et al. Observation of OH radicals produced by pulsed discharges on the surface of a liquid. Plasma Sources Science and Technology. 2011; 20 :034010. DOI: 10.1088/0963-0252/20/3/034010 - 26.
Hoffer P, Sugiyama Y, Hosseini SHR, Akiyama H, Lukes P, Akiyama M. Characteristics of meter-scale surface electrical discharge propagating along water surface at atmospheric pressure. Journal of Physics D: Applied Physics. 2016; 49 :415202. DOI: 10.1088/0022-3727/49/41/415202 - 27.
Xiong Y, Zhang Q, Wandell R, Bresch S, Wang H, Locke BR. Synergistic 1 , 4-dioxane removal by non-thermal plasma followed by biodegradation Synergistic 1,4-dioxane removal by non-thermal plasma followed by biodegradation. Chemical Engineering Journal. 2018; 361 :519-527. DOI: 10.1016/j.cej.2018.12.094 - 28.
Wandell RJ, Wang H, Bulusu RKM, Gallan RO, Locke BR. Formation of nitrogen oxides by nanosecond pulsed plasma discharges in gas – Liquid reactors. Plasma Chemistry and Plasma Processing. 2019; 39 :643-666. DOI: 10.1007/s11090-019-09981-w - 29.
Takahashi K, Konno R, Satta N, Takaki K. Estimation of hydroxyl radicals produced by pulsed discharge inside bubble in water using indigo carmine as chemical probe. IEEE Transactions on Plasma Science. 2018; 46 :663-669. DOI: 10.1109/TPS.2018.2792480 - 30.
Li J, Sato M, Ohshima T. Degradation of phenol in water using a gas–liquid phase pulsed discharge plasma reactor. Thin Solid Films. 2007; 515 :4283-4288. DOI: 10.1016/j.tsf.2006.02.070 - 31.
Takahashi K, Yagi I, Takaki K, Satta N. Development of pulsed discharge inside bubble in water. IEEE Transactions on Plasma Science. 2011; 39 :2654-2655. DOI: 10.1109/TPS.2011.2164095 - 32.
Takahashi K, Takayama H, Kobayashi S, Takeda M, Nagata Y, Karashima K, et al. Observation of the development of pulsed discharge inside a bubble under water using ICCD camera. Vacuum. 2020; 182 :109690. DOI: 10.1016/j.vacuum.2020.109690 - 33.
Sharma A, Levko D, Raja LL, Cha MS. Kinetics and dynamics of nanosecond streamer discharge in atmospheric-pressure gas bubble suspended in distilled water under saturated vapor pressure conditions. Journal of Physics D: Applied Physics. 2016; 49 :395205. DOI: 10.1088/0022-3727/49/39/395205 - 34.
Tachibana K, Takekata Y, Mizumoto Y, Motomura H, Jinno M. Analysis of a pulsed discharge within single bubbles in water under synchronized conditions. Plasma Sources Science and Technology. 2011; 20 :34005. DOI: 10.1088/0963-0252/20/3/034005 - 35.
Physics A, Sobota A, Universiteit T, Technische V, Eindhoven U, Philips M. Speed of streamers in argon over a flat surface of a dielectric. Journal of Physics D: Applied Physics. 2008; 42 :015211. DOI: 10.1088/0022-3727/42/1/015211 - 36.
Babaeva NY, Tereshonok DV, Naidis GV. Fluid and hybrid modeling of nanosecond surface discharges: effect of polarity and secondary electrons emission. Plasma Sources Science and Technology. 2016; 25 :044008. DOI: 10.1088/0963-0252/25/4/044008 - 37.
Bruggeman P, Guns P, Degroote J, Vierendeels J. Influence of the water surface on the glow-to-spark transition in a metal-pin-to-water electrode system. Plasma Sources Science and Technology. 2008; 17 :045014. DOI: 10.1088/0963-0252/17/4/045014 - 38.
Takahashi K, Takeda M, Konno R, Takaki K, Satta N. Influence of electric parameters on hydroxyl radical production by positive pulsed discharge inside of a bubble in water. IEEE Transactions on Plasma Science. 2019; 47 :1105-1113. DOI: 10.1109/TPS.2018.2883767 - 39.
Takahashi K, Mukaigawa S, Takaki K, Fujiwara T, Satta N. Water purification using non-thermal plasma driven by blumlein-line stacked pulsed power generator. Journal of Plasma and Fusion Research SERIES. 2009; 8 :1459-1462 - 40.
Minamitani Y, Yamada T. Investigation of the influence of droplets to streamer discharge in water treatment by pulsed discharge in air spraying. IEEE Transactions on Plasma Science. 2016; 44 :2173-2180. DOI: 10.1109/TPS.2016.2592515 - 41.
Stefanovic I, Bibinov N, Deryugin A, Vinoradov I, Napartovich A, Wiesemann K. Kinetics of ozone and nitric oxides in dielectric barrier discharges in O2/NOx and N2/O2/NOx mixtures. Plasma Sources Science and Technology. 2001; 10 :406-416. DOI: 10.1088/0963-0252/10/3/303 - 42.
Luo Y, Lietz AM, Yatom S, Kushner MJ, Bruggeman PJ. Plasma kinetics in a nanosecond pulsed filamentary discharge sustained in Ar – H2O and H2O. Journal of Physics D: Applied Physics. 2019; 52 :044003. DOI: 10.1088/1361-6463/aaeb14 - 43.
Liu Y, Tan Z, Chen X, Li X, Wang X. A numerical investigation on the effects of water vapor on electron energy and OH production in atmospheric-pressure He/H2O and Ar/H2O plasma jets. IEEE Transactions on Plasma Science. 2019; 47 :1593-1604. DOI: 10.1109/TPS.2019.2896060 - 44.
Shirafuji T, Murakami T. Contribution of electrons, Ar(3P0,2), H2O+, and H3O+ to production of OH(A2Σ+) in a micro-dielectric barrier discharge of Ar/H2O. Japanese Journal of Applied Physics. 2014; 54 :01AC03. DOI: 10.7567/JJAP.54.01AC03 - 45.
Verreycken T, Schram DC, Leys C, Bruggeman P. Spectroscopic study of an atmospheric pressure dc glow discharge with a water electrode in atomic and molecular gases. Plasma Sources Science and Technology. 2010; 19 :045004. DOI: 10.1088/0963-0252/19/4/045004 - 46.
Komuro A, Ono R, Oda T. Behaviour of OH radicals in an atmospheric-pressure streamer discharge studied by two-dimensional numerical simulation. Journal of Physics D: Applied Physics. 2013; 46 :175206. DOI: 10.1088/0022-3727/46/17/175206 - 47.
Bruggeman P, Liu J, Degroote J, Kong MG. DC excited glow discharges in atmospheric pressure air in pin-to-water electrode. Journal of Physics D: Applied Physics. 2008; 41 :215201. DOI: 10.1088/0022-3727/41/21/215201 - 48.
Wakisaka S, Tsuda K, Takahashi K, Satoh K. Mechanism of pH variation and H 2 O 2 generation in water exposed to pulsed discharge plasma. IEEE Transactions on Plasma Science. 2019; 47 :1083-1088. DOI: 10.1109/TPS.2018.2866282 - 49.
Atkinson R, Baulch DL, Cox RA, Hampson RF, Kerr JA, Troe J. Evaluated kinetic and photochemical data for atmospheric chemistry: Supplement III. IUPAC subcommittee on gas kinetic data evaluation for atmospheric chemistry. Journal of Physical and Chemical Reference Data. 1989; 18 :881. DOI: 10.1063/1.555832 - 50.
Gerasimov GY, Shatalov OP. Kinetic mechanism of combustion of hydrogen–oxygen mixtures. Journal of Engineering Physics and Thermophysics. 2013; 86 :987-995. DOI: 10.1007/s10891-013-0919-7 - 51.
Yagi I, Ono R, Oda T, Takaki K. Two-dimensional LIF measurements of humidity and OH density resulting from evaporated water from a wet surface in plasma for medical use. Plasma Sources Science and Technology. 2014; 24 :015002. DOI: 10.1088/0963-0252/24/1/015002 - 52.
Takeuchi N, Ando M, Yasuoka K. Investigation of the loss mechanisms of hydroxyl radicals in the decomposition of organic compounds using plasma generated over water. Japanese Journal of Applied Physics. 2015; 54 :116201. DOI: 10.7567/JJAP.54.116201 - 53.
Chen C, Liu DX, Liu ZC, Yang AJ, Chen HL, Shama G, et al. A model of plasma-biofilm and plasma-tissue interactions at ambient pressure. Plasma Chemistry and Plasma Processing. 2014; 34 :403-441. DOI: 10.1007/s11090-014-9545-1 - 54.
Rumbach P, Bartels DM, Go DB. The penetration and concentration of solvated electrons and hydroxyl radicals at a plasma-liquid interface. Plasma Sources Science and Technology. 2018; 27 :115013. DOI: 10.1088/1361-6595/aaed07 - 55.
Kanazawa S, Kawano H, Watanabe S, Furuki T, Akamine S, Ichiki R, et al. Observation of OH radicals produced by pulsed discharges on the surface of a liquid. Plasma Sources Science and Technology. 2011; 20 :34010. DOI: 10.1088/0963-0252/20/3/034010 - 56.
Gomes A, Fernandes E, Lima JLFC. Fluorescence probes used for detection of reactive oxygen species. Journal of Biochemical and Biophysical Methods. 2005; 65 :45-80. DOI: 10.1016/j.jbbm.2005.10.003 - 57.
Shiraki D, Ishibashi N, Takeuchi N. Quantitative estimation of OH radicals reacting in liquid using a chemical probe for plasma in contact with liquid. IEEE Transactions on Plasma Science. 2016; 44 :3158-3163. DOI: 10.1109/TPS.2016.2603157 - 58.
Knipping EM, Dabdub D. Modeling Cl2 formation from aqueous NaCl particles: Evidence for interfacial reactions and importance of Cl2 decomposition in alkaline solution. Journal of Geophysical Research. 2002; 107 :4360. DOI: 10.1029/2001JD000867 - 59.
Yuchen H, Uehara S, Tanaka H, Nishiyama H. Numerical modelling and simulation of chemical reactions in a nano-pulse discharged bubble for water treatment. Plasma Science and Technology. 2016; 18 :924-934. DOI: 10.1088/1009-0630/18/9/09 - 60.
Ono R, Oda T. Dynamics of ozone and OH radicals generated by pulsed corona discharge in humid-air flow reactor measured by laser spectroscopy. Journal of Applied Physics. 2003; 93 :5876-5882. DOI: 10.1063/1.1567796 - 61.
Nakagawa Y, Ono R, Oda T. Effect of discharge polarity on OH density and temperature in coaxial-cylinder barrier discharge under atmospheric pressure humid air. Japanese Journal of Applied Physics. 2018; 57 :096103. DOI: 10.7567/JJAP.57.096103 - 62.
Staehelln J, Holgne J. Decomposition of ozone in water: Rate of initiation by hydroxide ions and hydrogen peroxide. Environmental Science & Technology. 1982; 16 :676-681. DOI: 10.1021/es00104a009 - 63.
Kim HH, Prieto G, Takashima K, Katsura S, Mizuno A. Performance evaluation of discharge plasma process for gaseous pollutant removal. Journal of Electrostatics. 2002; 55 :25-41. DOI: 10.1016/S0304-3886(01)00182-6 - 64.
Soloshenko IA, Tsiolko VV, Pogulay SS, Kalyuzhnaya AG, Bazhenov VY, Shchedrin AI. Effect of water adding on kinetics of barrier discharge in air. Plasma Sources Science and Technology. 2009; 18 :045019. DOI: 10.1088/0963-0252/18/4/045019 - 65.
Machala Z, Tarabova B, Hensel K, Spetolikova E, Sikurova L, Lukes P. Formation of ROS and RNS in water electro-sprayed through transient spark discharge in air and their bactericidal effects. Plasma Processes and Polymers. 2013; 10 :649-659. DOI: 10.1002/ppap.201200113 - 66.
Régimbal JM, Mozurkewich M. Peroxynitric acid decay mechanisms and kinetics at low pH. The Journal of Physical Chemistry. A. 1997; 101 :8822-8829. DOI: 10.1021/jp971908n - 67.
Warneck P. Chemical reactions in clouds. Fresenius' Journal of Analytical Chemistry. 1991; 340 :585. DOI: 10.1007/BF00322434 - 68.
Hoigne J, Bader H, Haag WR, Staehelin J. Rate constants of reactions of ozone with organic and inorganic compounds in water—III. Inorganic compounds and radicals. Water Research. 1985; 19 :993-1004. DOI: 10.1016/0043-1354(85)90368-9 - 69.
Takahashi K, Kawamura S, Takada R, Takaki K, Satta N, Fujio T. Influence of a plasma-treated nutrient solution containing 2,4-dichlorobenzoic acid on the growth of cucumber in a hydroponic system. Journal of Applied Physics. 2021; 129 :143301. DOI: 10.1063/5.0044328 - 70.
Hug SJ, Leupin O. Iron-catalyzed oxidation of Arsenic(III) by oxygen and by hydrogen perxide: pH-dependent formation of oxidants in the fenton reaction. Environmental Science & Technology. 2003; 37 :2734-2742. DOI: 10.1021/es026208x - 71.
Kremer ML. Mechanism of the Fenton reaction. Evidence for a new intermediate. Physical Chemistry Chemical Physics. 1999; 1 :3595-3605. DOI: 10.1039/A903915E - 72.
White EM, Vaughan PP, Zepp RG. Role of the photo-Fenton reaction in the production of hydroxyl radicals and photobleaching of colored dissolved organic matter in a coastal river of the southeastern United States. Aquatic Sciences. 2003; 65 :402-412. DOI: 10.1007/s00027-003-0675-4 - 73.
Takahashi K, Takaki K, Satta N. Water remediation using pulsed power discharge under water with advanced oxidation process. Journal of Advanced Oxidation Technologies. 2012; 15 :365-373. DOI: 10.1515/jaots-2012-0216 - 74.
Liu Q, Schurter LM, Muller CE, Aloisio S, Francisco JS, Margerum DW. Kinetics and mechanisms of aqueous ozone reactions with bromide, sulfite, hydrogen sulfite, iodide, and nitrite ions. Inorganic Chemistry. 2001; 40 :4436-4442. DOI: 10.1021/ic000919j - 75.
Buxton GV, Greenstock CL, Helman WP, Ross AB. Critical review of rate constants for reactions of hydrated electrons, hydrogen atoms and hydroxyl radicals in aqueous solution. Journal of Physical and Chemical Reference Data. 1987; 17 :513. DOI: 10.1063/1.555805 - 76.
Ross F, Ross AB. Selected specific rates of reactions of transients from water in aqueous solution. In: III. Hydroxyl Radical and Perhydroxyl Radical and Their Radical Ions. United States: N: Web; 1977. DOI: 10.2172/6635906 - 77.
Logan SR. Redox reactions of organic radicals with ferrocene/ferricenium species in aqueous solution. Part 1. Radicals derived from carboxylic acids. Journal of the Chemical Society, Perkin Transactions. 1989; 2 :751-754. DOI: 10.1139/v91-081 - 78.
Hoigne J, Bader H. Rate constants of reactions of ozone with organic and inorganic compounds in waterII Dissociating organic compounds. Water Research. 1983; 17 :158-194. DOI: 10.1016/0043-1354(83)90098-2 - 79.
Neta P, Huie RE, Ross AB. Rate constants for reactions of inorganic radicals in aqueous solution rate · constants for reactions of inorganic radicals in aqueous solution. Journal of Physical and Chemical Reference Data. 2009; 17 :1027-1284. DOI: 10.1063/1.555808 - 80.
Abe A. Distribution of 1, 4-dioxane in relation to possible sources in the water environment. Science of the Total Environment. 1999; 227 :41-47. DOI: 10.1016/S0048-9697(99)00003-0 - 81.
Zenker MJ, Borden RC, Barlaz MA. Occurrence and treatment of 1,4-dioxane in aqueous environments. Environmental Engineering Science. 2003; 20 :423-443. DOI: 10.1089/109287503768335913 - 82.
Khan FI, Ghoshal AK. Removal of volatile organic compounds from polluted air. Journal of Loss Prevention in the Process Industries. 2000; 13 :527-545. DOI: 10.1016/S0950-4230(00)00007-3 - 83.
Huang B, Lei C, Wei C, Zeng G. Chlorinated volatile organic compounds (Cl-VOCs) in environment — sources, potential human health impacts, and current remediation technologies. Environment International. 2014; 71 :118-138. DOI: 10.1016/j.envint.2014.06.013 - 84.
Bian W, Song X, Liu D, Zhang J, Chen X. Actions of nitrogen plasma in the 4-chrolophenol degradation by pulsed high-voltage discharge with bubbling gas. Chemical Engineering Journal. 2013; 219 :385-394. DOI: 10.1016/j.cej.2012.12.074 - 85.
Nunnally T, Tsangaris A, Rabinovich A, Nirenberg G. Gliding arc plasma oxidative steam reforming of a simulated syngas containing naphthalene and toluene. International Journal of Hydrogen Energy. 2014; 39 :11976-11989. DOI: 10.1016/j.ijhydene.2014.06.005 - 86.
Yang J, Zeng D, Hassan M, Ma Z, Dong L, Xie Y, et al. Efficient degradation of Bisphenol A by dielectric barrier discharge non-thermal plasma: Performance, degradation pathways and mechanistic consideration. Chemosphere. 2021; 286 :131627. DOI: 10.1016/j.chemosphere.2021.131627 - 87.
Lei W, Huifen Z, Xin Y. Dechlorination and decomposition of trichloroacetic acid by glow discharge plasma in aqueous solution. Electrochimica Acta. 2014; 115 :332-336. DOI: 10.1016/j.electacta.2013.10.160 - 88.
Ghodbane H, Hamdaoui O, Vandamme J, Durme JV, Vanraes P, Leys C, et al. Degradation of AB25 dye in liquid medium by atmospheric pressure non-thermal plasma and plasma combination with photocatalyst TiO2. Open Chemistry. 2014; 13 :325-331. DOI: 10.1515/chem-2015-0040 - 89.
Shirafuji T, Ishida Y, Nomura A, Hayashi Y, Goto M. Reaction mechanisms of methylene-blue degradation in three-dimensionally integrated micro-solution plasma. Jpn. Journal of Applied Physics. 2017; 56 :06HF02. DOI: 10.7567/JJAP.56.06HF02 - 90.
Iwabuchi M, Takahashi K, Takaki K, Satta N. Influence of sodium carbonate on decomposition of formic acid by pulsed discharge plasma inside bubble in water. Japanese Journal of Applied Physics. 2016; 55 :07LF02. DOI: 10.7567/JJAP.55.07LF02 - 91.
Takahashi K, Takayama H, Yagi I, Takaki K, Satta N. Decomposition process of volatile organic compounds dissolved into water by pulsed discharge inside bubble. Japanese Journal of Applied Physics. 2020; 59 :SHHA06. DOI: 10.35848/1347-4065/ab72cd - 92.
Reife A, Freeman HS. Environmental Chemistry of Dyes and Pigments. New York, NY: John Wiley & Sons; 1996. pp. 50-59 - 93.
Backett MA, Hua I. Elucidation of the 1,4-dioxane decomposition pathway at discrete ultrasonic frequencies. Environmental Science & Technology. 2000; 34 :3944-3953. DOI: doi.org/10.1021/es000928r - 94.
Stefan MI, Bolton JR. Mechanism of the degradation of 1,4-dioxane in dilute aqueous solution using the UV/hydrogen peroxide process. Environmental Science & Technology. 1998; 32 :1588-1595. DOI: 10.1021/es970633m - 95.
Höbel B, Sonntag C. OH-Radical induced degradation of ethylenediaminetetraacetic acid(EDTA) in aqueous solution; a pulse raiolysis study. Journal of the Chemical Society, Perkin Transactions. 1998; 2 :509-513. DOI: 10.1039/A708167G - 96.
Thomas JK. Rates of reaction of the hydroxyl radical. Transactions of the Faraday Society. 1966; 61 :702. DOI: 10.1039/TF9656100702 - 97.
Haag WR, Yao CCCD. Rate constants for reaction off hydroxyl radicals with several drinking water contaminants. Environmental Science & Technology. 1992; 26 :1005-1013. DOI: 10.1021/es00029a021 - 98.
Fitzsimmons C, Ismail F, Whitehead JC, Wilman JJ. The chemistry of dichloromethane destruction in atmospheric-pressure gas streams by a dielectric packed-bed plasma reactor. The Journal of Physical Chemistry. A. 2000; 104 :6032-6038. DOI: doi.org/10.1021/jp000354c - 99.
Kundu SK, Kennedy EM, Mackie JC, Holdsworth CI, Molloy TS, Gaikwad VV, et al. Study on the reaction of CCl2F2 with CH4 in a dielectric barrier discharge nonequilibrium plasma. Plasma Processes and Polymers. 2013; 10 :912-921. DOI: 10.1002/ppap.201300053 - 100.
Gaikwad V, Kennedy E, Mackie J, Holdsworth C, Molloy S, Kundu S, et al. Reaction of dichloromethane under non-oxidative conditions in a dielectric barrier discharge reactor and characterisation of the resultant polymer. Chemical Engineering Journal. 2016; 290 :499-506. DOI: 10.1016/j.cej.2015.12.105 - 101.
Orlandini I, Riedel U. Chemical kinetics of NO removal by pulsed corona discharges. Journal of Physics D: Applied Physics. 2000; 33 :2467 - 102.
Takaki K, Takahashi K, Hamanaka D, Yoshida R, Uchino T. Function of plasma and electrostatics for keeping quality of agricultural produce in post-harvest stage. Japanese Journal of Applied Physics. 2021; 60 :010501. DOI: 10.35848/1347-4065/abcc13 - 103.
Takaki K, Hayashi N, Wang D, Ohshima T. High-voltage technologies for agriculture and food processing. Journal of Physics D: Applied Physics. 2019; 52 :473001. DOI: 10.1088/1361-6463/ab2e2d - 104.
Puac N, Gherardi M, Shiratani M. Plasma agriculture : A rapidly emerging field. Plasma Processes and Polymers. 2018; 15 :1700174. DOI: 10.1002/ppap.201700174 - 105.
Ranieri P, Kizer J, Gatiboni L, Hernández R, Pierce MR, Stapelmann K, et al. Plasma agriculture : Review from the perspective of the plant and its ecosystem. Plasma Processes and Polymers. 2020; 18 :e2000162. DOI: 10.1002/ppap.202000162 - 106.
Okumura T, Saito Y, Takano K, Takahashi K, Takaki K, Satta N, et al. Inactivation of bacteria using discharge plasma under liquid fertilizer in a hydroponic culture system. Plasma Medicine. 2017; 6 :247-254. DOI: 10.1615/PlasmaMed.2016018683 - 107.
Takahata J, Takaki K, Satta N, Takahashi K. Improvement of growth rate of plants by bubble discharge in water. Japanese Journal of Applied Physics. 2015; 54 :01AG07. DOI: 10.7567/JJAP.54.01AG07 - 108.
Takahashi K, Saito Y, Oikawa R, Okumura T, Takaki K, Fujio T. Development of automatically controlled corona plasma system for inactivation of pathogen in hydroponic cultivation medium of tomato. Journal of Electrostatics. 2018; 91 :61-69. DOI: 10.1016/j.elstat.2017.12.006 - 109.
Schnabel U, Andrasch M, Weltmann K. Antimicrobial efficiency of non-thermal atmospheric pressure plasma processed water (PPW) against agricultural relevant bacteria suspensions. International Journal of Environmental & Agriculture Research. 2016; 2 :212-224 - 110.
Ma R, Wang G, Tian Y, Wang K, Zhang J, Fang J. Non-thermal plasma-activated water inactivation of food-borne pathogen on fresh produce. Journal of Hazardous Materials. 2015; 300 :643-651. DOI: 10.1016/j.jhazmat.2015.07.061 - 111.
Xu Y, Tian Y, Ma R, Liu Q, Zhang J. Effect of plasma activated water on the postharvest quality of button mushrooms, Agaricus bisporus. Food Chemistry. 2016; 197 :436-444. DOI: 10.1016/j.foodchem.2015.10.144 - 112.
Andrasch M, Stachowiak J, Schlüter O, Schnabel U, Ehlbeck J. Scale-up to pilot plant dimensions of plasma processed water generation for fresh-cut lettuce treatment. Food Packaging and Shelf Life. 2017; 14 :40-45. DOI: 10.1016/j.fpsl.2017.08.007