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Martin De Vidales, M.J. Aqueous Organic Pollutants. Encyclopedia. Available online: (accessed on 17 June 2024).
Martin De Vidales MJ. Aqueous Organic Pollutants. Encyclopedia. Available at: Accessed June 17, 2024.
Martin De Vidales, Maria Jose. "Aqueous Organic Pollutants" Encyclopedia, (accessed June 17, 2024).
Martin De Vidales, M.J. (2021, January 18). Aqueous Organic Pollutants. In Encyclopedia.
Martin De Vidales, Maria Jose. "Aqueous Organic Pollutants." Encyclopedia. Web. 18 January, 2021.
Aqueous Organic Pollutants

Advanced oxidation processes (AOPs) are regarded as effective techniques for organic contaminants removal from water and wastewater.

graphitic carbon nitride AOPs

1. Introduction

In recent years, environmental pollution, especially water pollution, is increasingly becoming a major concern worldwide. Many organic pollutions, such as pharmaceuticals and personal care products (PPCPs), pesticides, and organic dyes are toxic and refractory [1][2][3][4]. Various techniques have been developed to eliminate aqueous organic pollutants (e.g., extraction, adsorption, biological treatment, and advanced oxidation processes) [5][6][7][8][9]. Advanced oxidation processes (AOPs) are regarded as effective techniques for organic contaminants removal from water and wastewater [10][11][12][13][14].

The AOPs utilize highly reactive species (mainly hydroxyl radical, •OH) to oxide the organic pollutants into less toxic or no-toxic products such as CO2 and H2O [15][16]. According to supplied energies and reactive species, AOPs can be categorized as photocatalysis, electrocatalysis, sonolysis, ozonation, Fenton/Fenton-like reactions, and sulfate radical-based AOPs (SR-AOPs), among others [17][18]. In recent decades, numerous studies have been conducted to develop novel AOPs. Emerging energy sources (e.g., ionizing radiation with electron beams and γ-radiolysis, pulsed plasma, etc.) were applied, and different reactive species (such as periodate or ferrate reagent) were introduced [19][20][21][22]. Considering the merits of different AOPs, combinations of various processes are more common approaches to enhance degradation efficiency [21]. Although some AOPs (e.g., UV/H2O2, UV/peroxymonosulfate (PMS)) work properly without catalysts, employing catalysts can significantly reduce energy and reagent (source of reactive species) consumption [23]. Therefore, designing an effective and stable catalyst is a crucial strategy for the development of AOPs.

Graphic carbon nitride (g-C3N4), known as a metal-free polymer semiconductor, has attracted increasing attention due to its unique electronic band structure, anti-photocorrosion, excellent physicochemical stability, and easy availability [24][25]. The bandgap of g-C3N4 is about 2.7 eV, which enables it to absorb all viewing range of solar irradiation. The valance band (VB) and conduction band (CB) mainly encompass nitrogen and carbon pz orbitals while VB top and CB bottom are located at about +1.4 and −1.3 eV, respectively [26][27][28]. The study of g-C3N4 can be traced back to 1834, when Berzelius first synthesized a polymeric derivative of g-C3N4, and Liebig named it melon [29]. In 2006, Goettmann and his co-workers investigated Friedel–Crafts reactions that can be catalyzed by g-C3N4, which is its first application in the catalytic field [30]. In 2009, g-C3N4 was demonstrated as a good metal-free photocatalyst for water splitting by Wang et al. [26]. Up to now, g-C3N4 has been in-depth studied and extensively applied in photocatalysis. The g-C3N4 preparation relies on (solvo)thermal polymerization of nitrogen-rich precursors such as melamine, dicyandiamide, and urea [31]. In addition, hard/soft temple-assisted methods and sol-gel methods are frequently used to modify the synthesis approaches. The reaction parameters such as precursors and temperature could significantly affect the physicochemical property, including specific surface area, bandgap, etc. [32]. However, the pure g-C3N4 encounters several drawbacks, including tiny surface area, inefficient use of visible light, low electric conductivity, and fast recombination of photo-induced carriers, which are not beneficial to its catalytic activity [33][34]. To address these issues, a lot of efforts such as (1) engineering the nanostructure of g-C3N4 [27][35][36][37], (2) introducing heteroatoms (metals [38][39][40][41][42][43][44] or non-metals [45][46][47][48][49][50]), (3) coupling with other semiconductors [51][52][53][54][55][56][57] and (4) co-polymerization [58][59][60][61] were made. g-C3N4 based composites hold unique advantages for organic pollutants removal from groundwater and wastewater due to the good adsorption capacity of g-C3N4 for organic molecules, which could be attributed to strong intermolecular forces like hydrogen bonding, π-π interactions between pollutant molecules and residual amino groups in the g-C3N4 fragment [62][63]. On the other hand, introducing extra sources of reactive species such as H2O2 or PMS in photocatalysis can significantly increase degradation efficiency [64][65]. Furthermore, some studies have explored g-C3N4 based composites for organic pollutants removal without light irradiation in the presence of PMS or H2O2 [66][67][68][69].

Some excellent reviews on g-C3N4 based composites involving pollution remediation have been published [25][31][70][71]. g-C3N4 based composites as photocatalysts for water purification have been summarized in these reviews, while no reviews involve other AOPs such as chemical AOPs and electrochemical AOPs. The dramatically increasing amounts of g-C3N4 based composites in the range of AOPs fields requires a broader, thorough, and up-date assessment.

2. Chemical AOPs

The chemical AOPs started as early as the application of the Fenton reaction to water treatment, in which •OH can be generated from the catalytic decomposition of H2O2 by Fe2+ for the destruction of various organic pollutants (Equation (1)) [10].

Fe2+ + H2O2 + H+ → Fe3+ + •OH + H2O

With the increasing demand for water treatment, various oxidants such as O3, PMS, peroxydisulfate (PDS) were applied in chemical AOPs. The PMS and PDS could be heterogeneous activated, and reactive species such as •SO4 are subsequently generated to degrade organic pollutants [72][73][74]. Table 1 summarizes the part of a representative study using g-C3N4 based composites as a catalyst in chemical AOPs.

Table 1. Graphic carbon nitride (g-C3N4) based composites for chemical advanced oxidation processes (AOPs).

Pure g-C3N4 holds inert activation performance of oxidants such as H2O2 and PMS. Considering that g-C3N4 has excellent affinity to entrap transition metal ions, metal doping is the main strategy for improving the catalytic activity. Oh et al. investigated the catalytic activities of Me-doped g-C3N4 (Me = Cu, Co, and Fe) as PMS activator for sulfathiazole degradation. Among the prepared catalyst, Co-doped g-C3N4 (0.59 wt% Co) exhibited the highest degradation efficiency for sulfathiazole, while excessive metal doping and surface defects (-C≡N) had a scavenging effect for •SO4 [91]. The authors further studied Fe-doped g-C3N4 for acid orange 7 degradation, and the non-radical pathway was proposed [84]. Li et al. prepared Fe doped g-C3N4 as PMS activator for phenolic compounds degradation. (Fe (V) = O) generated from the oxidation of Fe(III)-N was proposed as dominant reactive species [67]. In another work, Fe doped g-C3N4 was also employed in PMS activation for phenol degradation. Authors investigated the ratio of 46% and 54% of Fe (III) and Fe (II) via Mössbauer spectra, while the XPS survey spectra suggested the primary Fe on the surface of the catalyst was in the 3+ state. It was proposed that the Fe (II) complex heterolyzed at the O-O bond of activated PMS to form Fe (IV) = O, which was the primary active species [89]. In PMS/Mn-doped g-C3N4 system, superoxide radical was firstly generated due to the PMS bounding to the Mn-N site, and singlet oxygen produced by superoxide radical was proposed as the responsible reactive species for acetaminophen degradation [80]. Ma et al. synthesized Cu (I)-doped g-C3N4 for the removal of rhodamine B in a Fenton-like reaction. Cu (I) could be firmly embedded in g-C3N4 and reactive species produced by the interaction of H2O2 and Cu (I) [81]. The unique adsorption capacity of g-C3N4 for some organic pollutants also leads to superior degradation performance. Xie et al. investigated that different monochlorophenols isomers (2-chlorophenol, 3-chlorophenol, and 4-chlorophenol) could be degraded efficiently using Co-doped g-C3N4 as a catalyst in the presence of PMS. It was confirmed that the degradation rate was in the same order as the adsorption quantity [79]. This was attributed to the strong intermolecular forces between pollutant molecules and residual amino groups in the g-C3N4 fragment [92]. Pd-doped g-C3N4 was successfully synthesized by anchoring Pd nanoparticles on g-C3N4 using KBH4 reduction method, which was regularly active for PMS activation toward bisphenol A removal [82]. Metal oxide such as manganese oxide [85][90] and iron oxide [68] decorated on g-C3N4 are also employed for organic pollutions degradation via activating H2O2 or PMS (Figure 1). Lyu et al. prepared Cu (II)/CuAlO2/g-C3N4 composite as a Fenton-like catalyst. The Cu and C were investigated as dual reaction centers, and C-O-Cu acts as bridges to accelerating electrons transfer [75]. Nonmetal doping is also considered to be an efficient approach to improve electron transfer capability. Electronic structure modulation was achieved in oxygen-doped g-C3N4 for PMS activation, which was fabricated using urea and oxalic acid dihydrate [66]. The authors further investigated carbon and oxygen doped g-C3N4 exhibited better PMS activity due to its dual active sites-electron-poor C atoms and electron-rich O atoms [86]. Co-doping of iron and sulfur was found to be an approach to charge distribution and density of g-C3N4 for PMS activation [83]. To improve its chemical activity and electron transportation ability, Coupling nanocarbon materials g-C3N4 was developed to realize efficient PMS or H2O2 activation [87]. Moreover, combining nanocarbon materials and metal doping was frequently fabricated with g-C3N4 to exploit both materials’ synergistic effect [69][77][88].

Figure 1. (a) Schematic illustration of the catalytic mechanism of g-C3N4/CDs/Fe(II) in the presence of H2O2, reprinted with permission from [68]. Copyright 2019 American Chemical Society. (b) Proposed mechanism of PMS activation by gCN-Fe3 for AO7 removal, reprinted with permission from [83]. Copyright 2018 Elsevier.

3. Photochemical AOPs

Light irradiation is the most widely used method of applying additional energy to assist reactive species generating, which presents the advantages of simple, clean, relatively inexpensive, and efficient. TiO2 and ZnO were firstly used as photocatalysts for catalytic oxidation of organic contaminants. In this case, photocatalysis induces the formation of h+, •O2 and •OH, which act as principle reactive species for pollutants degradation. Consequently, visible light irradiations have been coupled with powerful oxidants such as H2O2 and PMS, including catalysis with a modified photocatalyst, resulting in various AOPs. In this section, the applications of these different AOPs as photocatalysis, Photo-Fenton (like) reactions, and photo-assisted sulfate radical based AOPs are summarized. Some representative applications of g-C3N4 based composites as a catalyst in photochemical AOPs are shown in Table 2.

Table 2. g-C3N4 based composites for photochemical AOPs.

3.1. Photocatalysis

As one typical technique of AOPs, photocatalytic degradation held the advantages of non-toxic, convenient operation, and high efficiency. With the irradiation of UV or visible light with energy larger than the semiconductor’s energy gap, the electron-donating and electron-accepting sites are formed in the surface of the semiconducting catalyst. The photogenerated electrons migrate from the valence band (VB) to the corresponding conduction band (CB), leaving holes in the VB, resulting in the electrons and holes occupying the CB and VB, respectively. Holes can directly oxidize pollutants or react with H2O/OH to produce hydroxyl radicals (Eθ(•OH/H2O) = 2.8 eV/NHE). Whereas the electrons capture dissolved oxygen (O2) to yield superoxide radical (Eθ(O2/•O2−) = −0.3 eV/NHE). The resulting •O2 are subsequently protonated to produce the •OH. Finally, those generated radicals take part in the oxidation of pollutants. In the early seventies, Fujishima and Honda showed the possibility of using the photo-excited semiconductor titanium dioxide (TiO2) to split water into hydrogen and oxygen in a photo-electrochemical solar cell [102]. This fundamental work led to developing a new AOP technology, based on semiconductor photocatalysis, for water purification.

g-C3N4 compounds have emerged as up-and-coming candidates to replace TiO2, owing to its graphite-like structure and medium bandgap [103][104]. However, the photocatalytic activity of g-C3N4 is still limited by its low electric conductivity and fast recombination of photo-induced carriers [105]. In this regard, modulating the nanostructure of g-C3N4 towards enhancing light harvest efficiency and catalytic mass-transfer is highly desirable. Researchers have made great efforts to design g-C3N4 with various structures, including 3D porous/nanospheres structure, 2D nanosheet and nanorod, etc. [27][37][106]. Such structures such as 3D porous and 2D nanosheet could provide high surface area, exposing more active sites for catalytic surface reactions. Furthermore, nanostructured g-C3N4 could significantly reduce photo-induced carriers’ transfer distance, leading to a lower recombination possibility. Moreover, the light quantum efficiencies could be significantly improved by constructing 0D, 1D nanorod, and 2D architectures g-C3N4 [107][108].

The VB top of g-C3N4 locates at about 1.4 V, leading to a small thermo-dynamic force for organic pollutants oxidation. Moreover, the more positive potential of •OH/H2O standard redox voltage results the hole cannot directly oxidize the H2O to generate •OH (Eθ(•OH/H2O) = 2.8 eV/NHE). To overcome this shortcoming, several elements of doping have been conducted [44][48][50][108]. Generally, metal doping occurs by inserting into the framework. In contrast, non-metal doping occurs in C or N atoms of g-C3N4 replaced by a heteroatom, which could enhance photocatalytic activity via improve the transfer and separation rates of photogenerated carriers and modulate bandgap [41][47]. Constructing heterojunction is another approach to enhance photodegradation performance for g-C3N4 [109][110]. Generally, Z-schemed heterojunction could be a good option that possesses higher redox potentials in forming reactive radicals and directly hole oxidation ability [111][112].

3.2. Photo-Fenton Like Processes

The Photo-Fenton process, the combination of ultraviolet or visible light with the conventional Fenton process, can enhance catalysts’ catalytic capacity and increase the degradation efficiency of organic pollutants and reduce iron sludge production [113]. The successive and competitive steps reaction mechanism for the photo-Fenton process are shown in Equations (2) and (3).

Fe2+ + H2O2 → Fe3+ + •OH + HO
Fe3+ + H2O + hv → •OH + Fe2+ + H+

As shown in Equation (2), Fe2+ rapidly reacts with H2O2 to generate Fe3+. The main form of Fe3+ is [Fe(OH)]2+ at pH 2.8–3.5, which plays a key role in reactions. Subsequently, the reduction of [Fe(OH)]2+ under light irradiation achieves redox recycling (Figure 2). Moreover, •OH can be generated via direct photolysis of H2O2 [16]. In the photo-Fenton process, the key is to accelerate the reduction of Fe3+ to Fe2+ via light irradiation. In the heterogeneous photo-Fenton reactions, the active sites’ redox cycle determines the reaction rate [114]. Although g-C3N4 cannot act as active sites for H2O2 decomposition, unique up conversion property, and substantial nitrogen coordinating sites make it become the ideal support for active sites [115]. In addition, the excellent photocatalytic activities of g-C3N4 based composites endue unique advantages as a catalyst for photo-Fenton-like reactions [116]. Metal doping into g-C3N4 is an important approach to enhance degradation efficiency in photo-Fenton reactions. Fe-doped g-C3N4 has been successfully synthesized by thermal shrinkage polymerization for aqueous organic pollutants degradation in photo-Fenton reactions. Introducing Fe in g-C3N4 accelerated the separation of photogenerated electron-holes. The Fe accepts electrons towards rapid reduction from trivalent to divalent, promoting the rapid generation of reactive species [117]. Another report about porous Fe-doped g-C3N4 revealed that the porous g-C3N4 structures enhance the photo-Fenton activity, owing to more active sites (Fe-N4) exposure [118]. An et al. embedded Fe into g-C3N4 by pyrolysis of Fe-N-containing precursor and melamine. The high-density Fe-Nx was investigated as a reactive site for H2O2 activation [119]. Another strategy used to realize efficient photo-Fenton-based degradation is heterojunction construction, including the Z scheme [120] and type II [121][122]. Zhang et al. prepared MnO2/Mn-modified alkalinized g-C3N4 by the calcination-impregnating method. It was proposed that Z-scheme charge transfer accelerated the redox cycle of the Mn4+/Mn3+/Mn2+ [123].

Figure 2. (a) schematic illustration of the catalytic mechanism of Fe2O3 QDs/g-C3N4-900 in H2O2/vis system, reprinted with permission from [113]. Copyright 2019 John Wiley & Sons, Inc. (b) Mechanism of photocatalytic degradation of atrazine with PMS, reprinted with permission from [96]. Copyright 2018 Elsevier.

3.3. Photo-Assisted Sulfate Radical Based AOPs

Sulfate radical-based advanced oxidation processes (SR-AOPs) are increasingly gaining attention as an effective solution to the destruction of recalcitrant organics in water [124]. Among various approaches to generate sulfate radicals via activation of additional sources of reactive species (such as peroxymonosulfate (PMS) and persulfate (PS)), the photo-activation in the presence of a heterogeneous catalyst is worth mentioning [65]. The general mechanism is presented in Equations (4)–(8).

Photocatalyst + hv → e + h+
S2O82− + e → SO42− + SO4-
HSO5 + e → SO4- + OH
HSO5 + h+ → SO5- + H+
2SO5- → 2SO4- + O2

Firstly, photocatalysts are excited under light irradiation to form photo-induced electrons and holes. Then the •SO4 and •OH are generated through the combination of electrons and PMS or PS. When transition metals are constructed into photocatalysts, they could be potential reactive sites for PMS/PS activation (shown in Equations (9)–(12)).

Mn+ + HSO5 → M(n+1)+ + SO4 + OH
M(n+1)+ + HSO5 → Mn+ + SO5 + H+
M(n+1)+ + e → Mn+
Mn+ + h+ → M(n+1)+

Similar to the application in photo-Fenton-like reactions, g-C3N4 generally plays as reactive site supporters or participate in heterojunction construction in photo-assisted sulfate radical based AOPs. The TiO2/g-C3N4 composite was fabricated for paracetamol photocatalytic degradation in the presence of visible light and persulfate. As prepared composite held type II heterojunction, which inhibits the electron-hole recombination in photocatalyst and adding persulfate increased 13 times degradation rate [94]. Liang et al. prepared porous 0D/3D NiCo2O4/g-C3N4 composite for carbamazepine removal. 99% of degradation was achieved in 10 min under visible light irradiation [93]. Jin et al. constructed Z-scheme MoS2/A g/g-C3N4 via a method of chemical electrostatic adsorption. The deposited Ag further enhances photocatalytic activity via improving light utilization ability and the separation rate of photogenerated e/h+ pairs. The results indicated that the presence of PMS dramatically accelerates the photocatalytic reaction [96]. Through metal ions such as Fe and Co doping, enhancing photocatalytic activity and improving PMS activation could synchronize implementation towards an efficient organic pollutant removal [95][98].


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