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. 2022 Jun 10;7(25):21418–21432. doi: 10.1021/acsomega.2c00512

Degradation of Organic Dyes Using the Ionizing Irradiation Process in the Presence of the CN/CD3/Fe6 Composite: Mechanistic Studies

Wen Li †, Qi Ye ‡, Tao Xia †, Long Zhao ‡,*, Miao Yang †,*
PMCID: PMC9244913  PMID: 35785285

Abstract

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Organic dyes are ubiquitous pollutants in various aquatic environments as they are produced in abundance and used widely. In the present work, the degradation and mineralization of various organic dyes such as methylene blue (MB), methyl orange (MO), and rhodamine B (RhB), following the electron beam irradiation method in the presence of a graphitic carbon nitride/carbon nanodots/Fe(II) (CN/CD3/Fe6) composite, were studied. The removal efficiency of MB reached 81.7% under conditions of electron beam irradiation (EBI) when the total irradiation dose was 5 kGy. This increased to 91.2% in the presence of the CN/CD3/Fe6 composite. The mineralization efficiency increased from 30.1 to 47.3% when the composite was added, and the total irradiation dose was 20 kGy. The removal efficiency of organic dyes was not significantly affected in the pH range of 3–11. Results from cyclic experiments conducted using MB degradation indicated that the CN/CD3/Fe6 composite exhibited good stability and reusability even after five irradiation cycles. Results from scavenging experiments revealed that •OH was the predominant reactive species during the MB degradation process. Intermediates produced in the synergistic system (EBI&CN/CD3/Fe6 system) consisting of the CN/CD3/Fe6 composite and EBI were detected using the liquid chromatography-mass spectrometry (LC-MS) technique. Based on the results, the possible degradation mechanism and pathways for MB were proposed.

1. Introduction

With the rapid development of the economy, industrial and agricultural water demand has increased. As a result, water pollution is becoming increasingly prominent. Tons of stable and persistent organic dyes are discharged annually by the textile, dyeing, and paper industries.1,2 This poses a risk to aquatic organisms and human beings. Hence, it is important to develop efficient dye treatment methods.3

Advanced oxidation processes (AOPs) are one of the promising technologies characterized by high degradation and mineralization efficiency for removing pollutants from water. Fenton oxidation, persulfate oxidation, ultrasonication, photocatalysis, ionizing irradiation, and other combined processes are associated with AOPs.4−7 Ionizing irradiation is an alternative technology used for treating wastewater. Electron beam irradiation (EBI) is an ionizing irradiation technique, and it is a rapid, efficient, and nonselective treatment method. Both oxidants (•OH, H2O2) and reductants (eaq–, •H, H2) can be produced through water radiolysis (eq 1), and these can degrade the target contaminants. The values in the brackets represent the radiation chemical yield (G-value) of each species (expressed in μmol/J) (including gamma ray and electron beam).8,9 However, it is worth mentioning that the safety issues about EBI and high cost of investment and operation are the main factors limiting its application. Besides, the intermediates produced during the EBI process require higher energy to mineralize. To improve the mineralization efficiency of organic pollutants and reduce operating costs, EBI is usually applied with addition of some oxidants like H2O2, ozone, persulfate, and the metal catalysts such as Fe2+ and TiO2.10−12

1. 1

Composites formed by graphitic carbon nitride (g-C3N4)/carbon nanodots (CDs) doped with metals have been extensively studied. These exhibit excellent photocatalytic efficiency during the process of organic pollutant degradation (dye and antibiotic).13−15 g-C3N4 is a low-cost photocatalyst capable of generating H2 and H2O2 from water, and CDs exhibit high catalytic activity during H2O2 decomposition. Liu et al. demonstrated that the combination of g-C3N4 and CDs exhibited a synergism on the processes of H2O2 decomposition and •OH production in the absence of light irradiation.16 Moreover, the doping of metals and metal oxides can further catalyze the degradation of organic pollutants. Chen et al. prepared the composite formed by g-C3N4/CDs doped with metal oxides. They demonstrated that the composite significantly enhanced photodegradation activity toward organic dyes RhB and MB.17 Fang et al. proposed the composite formed by graphitic carbon nitride/carbon nanodots doped with ferrous ions. They reported that the composite could significantly improve the organic dye removal efficiency under the Haber–Weiss reaction conditions to promote the generation of •OH and HO2• (eqs 2 and3).18 The composite is cost-efficient, can be easily prepared, and exhibits good cyclic degradation performance for organic dyes.19 This illustrates the excellent catalytic efficiency of the g-C3N4/CD composites doped with metals.

1. 2
1. 3

It is noticeable that numerous researchers have studied the process of removal of organic pollutants in homogeneous systems following the ionizing irradiation process.20−23 However, compared with homogeneous systems, a few studies have focused on heterogeneous systems. Yang et al. proposed a method using a combination of Fe/C nanomaterials and the ionizing irradiation method that could be used in the field of antibiotics degradation.11 Ma et al. demonstrated the degradation of organic dyes using the synergistic system consisting of g-C3N4 and ionizing irradiation.24 Chen et al. studied the degradation characteristic and mineralization efficiency of norfloxacin by ionizing irradiation technology combined with Fenton-like oxidation (magnetite and goethite).25 The high organic pollutant removal efficiencies were emphasized in all of the above reports. This suggested that ionizing irradiation could be potentially used for the degradation of organic pollutants present in heterogeneous systems. However, the reaction mechanism (for surface and solution reactions) associated with heterogeneous irradiation systems (the synergistic system consisting of a heterogeneous catalyst and ionizing irradiation) was not studied in these reports. Herein, the reaction mechanism associated with the system for a high concentration of organic dyes has been discussed in detail.

The degradation and mineralization of organic dyes in the synergistic system (EBI&CN/CD3/Fe6 system) consisting of the CN/CD3/Fe6 composite and EBI were studied. The paper reports the (a) efficiencies of the EBI system and homogeneous and heterogeneous EBI&CN/CD3/Fe6 systems used for the degradation and mineralization of organic dyes, (b) influence of solution pH, (c) stability and reusability of the CN/CD3/Fe6 composite, (d) main reactive species involved, (e) intermediates formed, and (f) degradation mechanism and pathways. New ideas for efficient degradation and mineralization of organic dyes have been proposed.

2. Experimental Section

2.1. Materials

Methylene blue trihydrate (MB, CAS [7220-79-3], ≥82.0%), rhodamine B (RhB, CAS [81-88-9], AR, ⩾98%), methyl orange (MO, CAS [547-58-0], ⩾98.5%), urea (CAS [57-13-6], ≥99%), citric acid monohydrate (CAS [5949-29-1], ⩾99.5%), iron(II) sulfate heptahydrate (CAS [7782-63-0], 99.0–100.0%), sodium hydroxide (CAS [1310-73-2], AR, ≥96%), hydrochloric acid (CAS [7647-01-0], GR), and sodium formate dihydrate (CAS [141-53-7], AR) were obtained from Sinopharm Chemical Reagent Co., Ltd. Tert-butanol (CAS [75-65-0], AR, ⩾99%) was obtained from Shanghai Macklin Biochemical Co., Ltd. Ultrapure water obtained from the EASY Ultrapure Water System (HealForce) was used for all of the studies.

2.2. Synthesis of the CN/CD3/Fe6 Composite

Citric acid (1.5 g) and urea (50 g) were mixed evenly into a crucible. The mixture was calcined at 550 °C for 3 h at a rate of 1 °C/min in a muffle furnace. Following this, it was cooled to room temperature (about 25 °C). Subsequently, the samples were washed, dried, and ground to obtain CN/CD3. The CN/CD3 solid powder (1.2 g) was mixed with 300 mL of 6 mM FeSO4 solution, and the mixture was stirred evenly. Following this, the mixture was ultrasonically dispersed into the suspension over 25 min. The mixture was stirred at a constant temperature of 60 °C to obtain the dried sample. The obtained sample was ground to form powder to obtain the target CN/CD3/Fe6 composite.19

2.3. EBI Experiments

All irradiation processes were carried out using a 0.4 MeV electron accelerator (dose per pass: 0.84 kGy/pass) in the State Key Laboratory of Advanced Electromagnetic Engineering and Technology, School of Electrical and Electronic Engineering, Huazhong University of Science and Technology. The high voltage was set as 400 kV, and the current of electron beam was 2.1 mA in every pass. The speed of the conveyor was 10 m/min. The experiment of total organic carbon (TOC) was carried out using a 1.0 MeV electron accelerator (dose per pass: 5 kGy/pass) in the School of Hubei University of Science and Technology. The dose was measured by an FWT-60-00 film color developer dose tablet. All irradiation treatments were conducted in duplicate at room temperature. In the EBI&CN/CD3/Fe6 system, the CN/CD3/Fe6 composite was spiked into organic dyes to reach the conditions of adsorption equilibrium before irradiation (according to the preliminary experiments, adsorption equilibrium can be reached because of the adequate adsorption time). The irradiated samples (5 mL) were filtered using 0.22 μm syringe filters for further use.

2.4. Analytical Methods

The ultraviolet–visible spectroscopy (UV/vis) profiles were recorded using a UV-2700 system (Shimadzu, Japan). The profiles were analyzed to detect the concentration of the organic dyes. The absorption wavelengths corresponding to MB, MO, and RhB were determined to be 665, 464, and 554 nm, respectively, by scanning the maximum absorption peak. The three dyes were diluted within the standard curve range of 0–10 mg/L, and it was observed that the absorbance was closely related to the concentration of the organic dyes (R2 > 0.99). The TOC values of the organic dyes were determined using a TOC analyzer (HTY-CT1000B, China). The organic dye solutions were processed using the heavy metal digestion instrument from Hanon (SH230N, China). The iron ion concentration was detected using the inductively coupled plasma-optical emission spectrometry (ICP-OES) technique. The system used was obtained from Agilent Technologies Inc. (Agilent 5110). The specific surface area of the CN/CD3/Fe6 composite was determined by the Brunauer–Emmet–Teller (BET) method through the isothermal adsorption and desorption of high-purity N2 using a TriStar II 3020 analyzer (Micromeritics).

The physiochemical properties of the CN/CD3/Fe6 composite before and after EBI experiments were characterized using transmission electron microscopy (TEM), X-ray diffraction (XRD), Fourier transform infrared spectroscopy (FTIR), and X-ray photoelectron spectroscopy (XPS) techniques. The morphology was examined using a 200 kV TEM instrument purchased from JEOL (JEM-2100F, Japan). The crystal structure and phase were determined using an XRD instrument obtained from PANalytical B.V. (Empyrean, The Netherlands) (using Cu Kα irradiation (λ = 1.54 Å) in the 2θ range between 10 and 70° with a 0.013° step size), and the XRD data were processed using MDI Jade 6.5 software. The crystallite size was calculated by the Debye–Scherrer equation (eq 4).

2.4. 4

where the crystallite size is denoted by D, the shape factor is denoted by K (K = 0.9), the wavelength of Cu Kα irradiation is denoted by λ (λ = 0.154 nm), the FWHM of the sample diffraction peak is denoted by B, and the diffraction angle is denoted by θ. The functional group was identified using an FTIR machine obtained from Thermo Fisher Scientific (Nicolet 6700). The elemental composition and chemical states were analyzed using the XPS technique (Thermo Fisher Scientific, ESCALAB 250Xi). To neutralize the charge of the sample, the flood gun was used to improve the charging effect using the charging compensation. All peaks were calibrated against the C 1s peak at 284.8 eV,26 and the XPS data were processed using XPSPEAK41 software.

The irradiated samples were filtered using 0.22 μm syringe filters to filter out the CN/CD3/Fe6 composite. After that, the irradiated samples were put in an electric blast drying oven at 50 °C to concentrate them. Finally, the processed MB solution was identified using a high-performance liquid chromatography system obtained from Thermo Fisher Scientific (UltiMate 3000) and the mass spectrometer obtained from Bruker Daltonics Inc. (micrOTOF II, Germany). The LC-MS system was equipped with a Boston Green ODS LC column (5 μm, 4.6 × 250 mm2). The analysis was carried out under the electrospray ionization ion operating mode (positive). The mobile phase of MB consisted of a mixture of methanol and water (3:97, v/v). The flow rate was maintained at 1.0 mL min–1, the injected volume was 20 μL, and the temperature for the detector was kept at 25 °C.

3. Results and Discussion

3.1. BET Analysis of the CN/CD3/Fe6 Composite

The specific surface area and the pore-size distribution of the CN/CD3/Fe6 composite were calculated through the isothermal adsorption/desorption of high-purity nitrogen using the BET method (Figure 1). The CN/CD3/Fe6 composite showed type IV and H3-type hysteresis loops (Figure 1a), indicating the presence of mesopore structures. The Barrett–Joyner–Halenda pore-size distributions of the CN/CD3/Fe6 composite verified the assumption, and the pore sizes were mainly distributed below 20 nm (Figure 1b).27,28 The results suggested that the calculated specific surface area and the average pore diameter of the CN/CD3/Fe6 composite were 37.40 m2 g–1 and 20.98 nm, respectively. The specific surface area is higher than some reported g-C3N4-based materials.29,30 The porous structures and large specific surface area can provide more active sites for pollutant adsorption and degradation.

Figure 1.

Figure 1

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(a) Nitrogen adsorption–desorption isotherm and (b) pore-size distribution of the CN/CD3/Fe6 composite.

3.2. Degradation of Organic Dyes Using the EBI&CN/CD3/Fe6 System

3.2.1. Effect of Heterogeneous and Homogeneous Irradiation Systems on the Process of MB Degradation

The effect of heterogeneous and homogeneous irradiation systems on the process of degradation of MB was investigated (Figure 2). It is noticeable that the irradiation process started after adsorption equilibrium was reached in the presence of the CN/CD3/Fe6 composite and MB solution (adsorption equilibrium of MB was reached at 90 min during the preliminary experiment). The purpose of performing experiments under conditions of both the heterogeneous and homogeneous (filtering the heterogeneous solution containing the composite and MB before irradiation, unfiltered CDs, and dissolved iron species present in the solution) irradiation systems is to verify the presence of solution reaction and its contribution to the process of MB degradation. The ICP-OES technique was used to measure the concentration of the dissolved iron species to understand the process of leaching of iron ions and the reaction mechanism (Figure 3).19

Figure 2.

Figure 2

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Effect of the CN/CD3/Fe6 composite dosage on the MB degradation efficiency in the EBI&CN/CD3/Fe6 system: (a) heterogeneous irradiation, (b) homogeneous irradiation, and (c) comparison of G-value (dose: 5 kGy), [MB]0 = 500 mg/L, pH = 5.3.

Figure 3.

Figure 3

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Concentration of iron ions in the EBI&CN/CD3/Fe6 system under conditions of (a) homogeneous irradiation and (b) heterogeneous irradiation. [MB]0 = 500 mg/L, pH = 5.3.

Figure 2 shows the process of degradation of MB under conditions of different systems, and the normalized concentration (C/C0) was plotted against the irradiation dose (Figure 2a,b).

The MB removal efficiency of the EBI system was significantly lower than the MB removal efficiency of the system containing the CN/CD3/Fe6 composite. To be more specific, the removal efficiency of MB under conditions of EBI reached 81.7% at 5 kGy. The value increased to 89.6% under homogeneous irradiation and 91.2% under heterogeneous irradiation conditions. The results obtained using a homogeneous irradiation system were better than those obtained using the EBI system alone. This implied the existence of solution reactions. Although there was no statistically significant difference between the heterogeneous irradiation system and the homogeneous irradiation system (Figure 2c), the MB removal efficiency and G-value between the two systems still had a slight difference, and it is speculated that there may also be surface reactions in the heterogeneous irradiation system. The optimal solid–liquid ratio was found to be 10 mg/5 mL. This could be attributed to the highest removal efficiency and G-value recorded during the process of MB degradation. Further experiments for MB degradation will be carried out based on the optimal solid–liquid ratio.

The iron ion concentration (C[Fe]) in the EBI&CN/CD3/Fe6 system is presented in Figure 3. As can be seen, the C[Fe] recorded in the homogeneous irradiation system remained stable (Figure 3a) and that recorded in the heterogeneous irradiation system increased (Figure 3b) with an increase in the irradiation dose. The phenomenon could be attributed to the reaction mechanism and can be explained primarily on the basis of various aspects. (1) The C[Fe] in the homogeneous system remained stable, but the removal efficiency of MB recorded for the homogenous system was higher than that recorded for the EBI system devoid of additives (Figure 2b). This indicated that there were reactions that did not consume dissolved iron present in the solution. This can be attributed to the Haber–Weiss reactions (eqs 2 and 3), and the H2O2 (produced in situ during the process of water radiolysis) and iron species in the solution trigger the continuous generation of the •OH and HO2• radicals.18 In addition, the remaining CDs in the filtered solution can catalyze the decomposition of H2O2 to generate •OH. It may also be contributing factors for MB degradation.19 (2) The C[Fe] recorded for the heterogeneous irradiation system increased, and this could be attributed to the leaching of iron ions occurring during the irradiation process. The MB removal efficiency and G-value between the heterogeneous irradiation system and the homogeneous irradiation system were slightly different; this may be because both the solution and surface reactions occurred in the heterogeneous irradiation system. On the one hand, iron ions leached into the heterogeneous irradiation system. This enhanced the solution reactions. On the other hand, H2O2 (produced in situ during the process of water radiolysis) adsorbed on the surface of the CN/CD3/Fe6 composite can be able to react with the CDs of the CN/CD3/Fe6 composite to trigger the production of the surface-bound •OH radicals. However, a statistically significant difference was not observed between the two systems, and this indicates that the solution reactions play a dominant role during the MB degradation process.

In addition, it is quite clear that while the difference in CN/CD3/Fe6 composite dosage and the connected dissolution of iron differ significantly between the different solutions, the difference in removal efficiency is very small. This phenomenon occurred due to the relatively low content of H2O2 produced through water radiolysis, and CDs in the solutions are also contributing factors for MB degradation.

3.2.2. Degradation of RhB and MO in the Heterogeneous Irradiation System

Besides MB, the degradation of RhB and MO in the heterogeneous irradiation system was also studied. Results from preliminary experiments suggested that both RhB and MO reached adsorption equilibrium at 180 min. As shown in Figure 4, the adsorption performance of the CN/CD3/Fe6 composite for MO was higher than that for RhB. This can be potentially attributed to the strong electrostatic interactions between MO and the CN/CD3/Fe6 composite.31 During the irradiation process, the maximum removal efficiencies of RhB and MO reached 94.5 and 87.5%, respectively. It should be noted that the removal efficiency for RhB and MO in the heterogeneous irradiation system was higher than those recorded for the EBI system alone.

Figure 4.

Figure 4

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Effect of the CN/CD3/Fe6 composite dosage on (a, b (dose: 5 kGy)) RhB and (c, d (dose: 10.5 kGy)) MO degradation in the EBI&CN/CD3/Fe6 system under conditions of heterogeneous irradiation. [RhB]0 = 1000 mg/L, pH = 3.5. [MO]0 = 1000 mg/L, pH = 6.5.

In addition, based on the contribution of adsorption and irradiation in dye removal (eqs 5–7), the solid–liquid ratio when the irradiation contribution was the largest was selected as the optimal solid–liquid ratio from the study point of view.11

3.2.2. 5
3.2.2. 6
3.2.2. 7

where the initial concentration of dye is denoted by C0, the concentration of dye after adsorption was completed is denoted by C1, and the concentration of dye after the whole process of adsorption and irradiation was completed is denoted by C2. As shown in Figure 4b,d, the optimal solid–liquid ratios for RhB and MO were determined to be 10 mg/5 mL and 1 mg/5 mL, respectively. Further RhB and MO degradation experiments will be carried out based on the optimal solid–liquid ratio.

3.2.3. Effect of Solution pH on the Process of Organic Dyes Degradation

The effect of initial pH on the process of organic dyes degradation using the EBI&CN/CD3/Fe6 system was also explored (Figure 5). It is clear that alkaline conditions are more conducive to the adsorption of MB and RhB. Efficient MO adsorption could not be realized under alkaline conditions (pH = 10.9). This could be attributed to the combined effect of pKa of MO (3.4) and pHpzc of the CN/CD3/Fe6 composite (5.5). When the MO solution became strongly alkaline, the adsorption of MO is lower because of ionic interaction between the negatively charged CN/CD3/Fe6 composite surface and negatively charged MO molecule.32 The effect of pH on the degradation of the three dyes was not the same during the EBI process. There was a negative impact on MB degradation under strongly acidic and alkaline conditions. This could be attributed to the reactions of reactive species in the solution.33 The effect of pH was not obvious during the process of RhB degradation. In the pH range of 3.5–11.0, the removal efficiency of RhB was >93.0%. Under different pH conditions, the removal efficiency of MO reached approximately 75.0% at 10 kGy, but the degradation efficiency decreased at pH = 10.9. This can be attributed to the fact that when the solution is strongly alkaline, the surface charge of the CN/CD3/Fe6 composite and MO repel each other. Thus, the process of MO degradation was hindered.34

Figure 5.

Figure 5

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Effect of solution pH on (a) MB, (b) RhB, and (c) MO degradation in the EBI&CN/CD3/Fe6 system under conditions of heterogeneous irradiation. [MB]0 = 500 mg/L, [CN/CD3/Fe6]/V(MB) = 10 mg/5 mL. [RhB]0 = 1000 mg/L, [CN/CD3/Fe6]/V(RhB) = 10 mg/5 mL. [MO]0 = 1000 mg/L, [CN/CD3/Fe6]/V(MO) = 1 mg/5 mL.

In general, although different pH-dependent effects were observed for the three dyes within the pH range of 3–11, the efficiency in each case was acceptable. More specifically, MB, RhB, and MO have the lowest efficiency under alkaline conditions and reached 77.6, 93.7, and 62.4%, respectively. It is worth mentioning that the typical Fenton reaction is strictly limited to an impractically low pH (<4) as there is a production of a large mass of iron precipitates under neutral and alkaline conditions,35 and the heterogeneous irradiation system studied in this article was not pH limited as the typical Fenton oxidation. In addition, the highest removal efficiency for the three dyes was recorded under natural pH conditions. This can facilitate the practical application of the organic dye treatment method.

3.3. Mineralization of Organic Dyes

TOC is an important indicator of the degree of mineralization for organic matters. In this study, organic dyes were irradiated in two systems to assess the efficiency of TOC removal during the EBI process. The mineralization performance of MB, RhB, and MO in the EBI and EBI&CN/CD3/Fe6 systems is shown in Figure 6.

Figure 6.

Figure 6

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TOC values recorded for (a) MB, (b) RhB, and (c) MO solutions in the EBI system and EBI&CN/CD3/Fe6 systems under conditions of heterogeneous irradiation. [MB]0 = 1000 mg/L, [CN/CD3/Fe6]/V(MB) = 20 mg/5 mL, pH = 5.3. [RhB]0 = 2000 mg/L, [CN/CD3/Fe6]/V(RhB) = 20 mg/5 mL, pH = 3.5. [MO]0 = 1000 mg/L, [CN/CD3/Fe6]/V(MO) = 1 mg/5 mL, pH = 6.5.

The EBI&CN/CD3/Fe6 system exhibited a higher TOC removal efficiency for the three dyes compared to the EBI system. This suggested that the synergistic system consisting of EBI and the CN/CD3/Fe6 composite could be used to improve the decomposition of organic dyes and increase the removal efficiency of organic content in the solution. The TOC value gradually decreased with an increase in the irradiation dose (for the three dyes in the two systems). The increased TOC value for MO at 15 kGy in the EBI system can be potentially attributed to the byproducts produced during the irradiation process.36 The TOC value for RhB at 0 kGy in the EBI&CN/CD3/Fe6 system was higher than that recorded for the EBI system alone. This can be attributed to the remaining CDs in the filtered solution.

3.4. Cyclic Experiment Using the CN/CD3/Fe6 Composite for MB Degradation

Five cycles of MB degradation tests were performed to evaluate the stability and reusability of the CN/CD3/Fe6 composite. Following the process of EBI treatment, the CN/CD3/Fe6 composite was collected, washed, and dried. Following this, they were reutilized for the next irradiation experiment.

3.4.1. Characterization of the CN/CD3/Fe6 Composite

Characterization tests were performed using fresh and five-time irradiated CN/CD3/Fe6 composites, and the TEM, FTIR, XRD, and XPS techniques were used for sample characterization.

Analysis of the TEM images (Figure 7) revealed that the presence of iron (Figure 7a) and the random distribution of CDs on the CN/CD3/Fe6 composite (Figure 7b) could also be observed. The morphology of the CN/CD3/Fe6 composite before irradiation (Figure 7c,d) is consistent with previous works.19 The morphology of the CN/CD3/Fe6 composite hardly changed after five irradiation cycles (Figure 7e,f). This suggested that the CN/CD3/Fe6 composite remained stable after irradiation. This is beneficial for the process of reutilization.

Figure 7.

Figure 7

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TEM images recorded for the CN/CD3/Fe6 composite: fresh (a–d) and after five times of irradiation (e, f).

The FTIR spectral profiles of the CN/CD3/Fe6 composite before and after irradiation were recorded (Figure 8a). The peak appearing at 810 cm–1 represented the characteristic stretching vibration mode of the triazine units. The peaks in the region of 1200–1650 cm–1 were assigned to the stretching vibration of the C–N heterocycle, and the broad absorption bands appearing in the region of 3000–3500 cm–1 represented the stretching vibrational modes of the N–H units of the uncondensed amino groups.19,37 The position of the characteristic peak of the CN/CD3/Fe6 composite remained unchanged. This indicated that the functional group was stable after irradiation.

Figure 8.

Figure 8

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(a) FTIR, (b) XRD, and (c–f) XPS profiles recorded for the CN/CD3/Fe6 composite (before and after five irradiation cycles).

The XRD patterns (Figure 8b) exhibited the presence of three peaks at 17.5, 27.3, and 29° before irradiation. The crystallite size calculated by the Debye–Scherrer equation was 2.61 nm. The peak at 27.3° corresponded to the (002) planes of g-C3N4,38,39 and the intensities of the (002) g-C3N4 peak increased after irradiation. This can be potentially attributed to the decrease in the iron content on the surface of the CN/CD3/Fe6 composite.40 The peaks at 17.5° (1) and 29° (2) corresponded to the diffraction peaks of compounds containing Fe(II) and Fe(III), and the results were in agreement well with the PDF no. 36-0425 strand card. The peaks of iron ions almost disappeared after irradiation, and this could attribute to the leaching of iron ions during irradiation. However, according to the XRD patterns of the CN/CD3/Fe6 composite, the diffraction peaks related to CDs are absent due to their very low amount.41

The surface chemical states of the elements present in the CN/CD3/Fe6 composite (before and after irradiation) were confirmed using the XPS technique. The peak corresponding to Fe2p (after irradiation) was absent in the spectral profile recorded for the Survey and Fe2p (Figure 8c,d, respectively). Analysis of Figure 8d reveals that Fe(II) and Fe(III) were present on the CN/CD3/Fe6 composite (before irradiation). The results agreed well with the results obtained using the XRD technique. These results demonstrate that the Fe(II) species were partially oxidized to Fe(III) during the synthesis process,19 and most of the Fe units present on the surface of the CN/CD3/Fe6 composite got dissolved during the irradiation process. The N 1s spectra and C 1s spectral profiles are presented in Figure 8e,f, respectively. The fitting parameters were determined from the XPS spectral profiles (Table 1).42−46 The N 1s and C 1s spectral profiles were analyzed, and it was observed that the binding energy and percentage of the total area of the functional group after irradiation changed by different degrees. This indicated that the chemical surroundings of C and N were diversified.

Table 1. Fitting Parameters Obtained by the XPS Spectra: Binding Energy (eV) and Percentage of Total Area (%).
core level energy (eV) state %
Fe 2p before EBI Fe 2p3/2 710.5 Fe(II)  
712.9 Fe(III) Fe(II) 56.8
718.4 Fe(II) satellite  
Fe 2p1/2 723.6 Fe(II)  
725.7 Fe(III) Fe(III) 43.2
730.0 Fe(III) satellite  
after EBI none
N 1s before EBI 397.1 C–N–C 66.1
398.3 N-(C)3 16.6
399.2 C=N 17.3
after EBI 396.9 C–N–C 56.1
397.7 N-(C)3 9.5
398.5 C=N 34.4
C 1s before EBI 283.0 C–C 25.4
284.0 C–H 7.3
285.5 C=O 15.5
286.4 COOR 51.8
after EBI 283.3 C–C 35.9
284.4 C–H 15.5
285.5 C=O 15.5
286.5 COOR 33.1
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3.4.2. Cyclic Experiment of the CN/CD3/Fe6 Composite Used for MB Degradation

Before conducting the EBI experiment, the recycled CN/CD3/Fe6 composite was added to the MB solution with an initial concentration of 500 mg/L. The degradation and mineralization of MB were compared over five cyclic experiments. The iron ion concentration was measured after each experiment to explore the leaching ability of iron ions present on the CN/CD3/Fe6 composite.

As shown in Figure 9a, the adsorption performance of the CN/CD3/Fe6 composite changed slightly after five cycles of irradiation at the solid-to-liquid ratio of 10 mg/5 mL.

Figure 9.

Figure 9

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Cyclic experiments conducted using the CN/CD3/Fe6 composite in the EBI&CN/CD3/Fe6 system under conditions of heterogeneous irradiation. (a) Degradation of MB. [MB]0 = 500 mg/L, [CN/CD3/Fe6]/V(MB) = 10 mg/5 mL, pH = 5.3, (b) TOC removal in MB solution [MB]0 = 1000 mg/L, [CN/CD3/Fe6]/V(MB) = 20 mg/5 mL, pH = 5.3, (irradiation dose: 25 kGy), and (c) iron ion concentration.

A small drop in the removal efficiency of MB was observed after irradiation. The CN/CD3/Fe6 composite exhibited good catalytic activity during MB removal after five cycles; this indicates that the XPS technique may only detect the iron ions on the surface of the CN/CD3/Fe6 composite, and there are still iron ions inside that can participate the surface reactions. The TOC removal efficiency in MB solution reached 57.3% after the first irradiation cycle. Following this, the efficiency decreased markedly as the number of cycles increased (Figure 9b). As seen in Figure 9c, the C[Fe] in the solution dropped significantly, and this could be attributed to repeated washing processes after the first irradiation cycle. The results indicated that the solution reactions became weak after the first irradiation cycle. The decreased TOC removal efficiency of MB can be potentially attributed to the solution reactions.

3.5. Role of Various Reactive Species on the Process of MB Degradation

Experiments were carried out under four conditions to elucidate the contribution of the reactive species to the process of MB degradation (Table 2). The N2 saturated system was taken as the control group. In the O2 saturated system, O2 could react with the reductive species (eaq–, •H) (eqs 8 and 9). •OH was the main reactive species.47,48Tert-butanol (TBA) could scavenge •OH (eq 10), and the main reactive species in the N2 saturated + TBA system were eaq–, •H.49 The primary reactive species present in the N2 saturated + formate system was eaq–, and this could be attributed to the reactions occurring between formate and •OH and •H (eqs 11 and 12).22

3.5. 8
3.5. 9
3.5. 10
3.5. 11
3.5. 12

As shown in Figure 10, under conditions of 5 kGy irradiation, the removal efficiency of MB under conditions of the N2 saturated, O2 saturated, N2 saturated + TBA, and N2 saturated + formate systems reached 94.0, 93.6, 65.8, and 64.5%, respectively. The N2 saturated system exhibited the maximum removal efficiency for MB. The N2 saturated system and O2 saturated system were compared, and little difference in MB removal was observed between the two. This suggests that •OH is the predominant reactive species during the MB degradation process. The effects of eaq– and •H were negligible. The N2 saturated + TBA system was slightly more efficient than the N2 saturated + formate system used for MB removal. This indicated that •H plays an insignificant role in the process of MB degradation. In summary, the contribution of the main reactive species during the MB degradation process was of the order •OH > eaq– > •H.

Table 2. Major Reactive Species under Different Experimental Conditions.

experiment conditions major reactive species
N2 saturated •OH, eaq–, •H
N2 saturated + TBA eaq–, •H
N2 saturated + formate eaq–
O2 saturated •OH
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Figure 10.

Figure 10

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Degradation of MB in the EBI&CN/CD3/Fe6 system under conditions of heterogeneous irradiation under different atmospheric conditions in the presence and absence of scavengers. [MB]0 = 500 mg/L, [TBA] = 0.5 M, [Formate] = 0.5 M. [CN/CD3/Fe6]/V(MB) = 10 mg/5 mL, pH = 5.3.

It is worth mentioning that the effect of scavenger concentrations on the process of MB degradation using the EBI&CN/CD3/Fe6 system was also explored (Figure S1). The results showed that the concentrations of scavengers used in the experiment did not make a large difference in the MB removal efficiency, indicating that the scavenger concentration of 0.5 M was excessive, and this was enough to consume the target reactive species.

3.6. Mechanism of MB Degradation in the EBI&CN/CD3/Fe6 System

Based on the reported literature50,51 and the results of the present work, the degradation mechanism of MB in the EBI&CN/CD3/Fe6 system was proposed. Figure 11a presents three routes: (I) The radiolysis of water generates oxidants and reductants, such as •OH, eaq–, •H, and H2O2. (II) The Haber–Weiss reactions between H2O2 (produced in situ during the process of water radiolysis) and iron ions in the solution promote the formation of •OH. CDs in the solution can catalyze the decomposition of H2O2 to promote the production of •OH. (III) Finally, H2O2 (produced in situ during the process of water radiolysis) adsorbed on the surface of the CN/CD3/Fe6 composite reacts with the CDs of the CN/CD3/Fe6 composite to trigger the production of •OH. Regardless of the pathways (water radiolysis (I), solution reactions (II), or surface reactions (III)), the MB molecules could be degraded by these reactive species. Based on the mechanism presented and the identified intermediates in the MB solution (the m/z value of the detected intermediates and the corresponding chemical structures are shown in Table 3), the possible MB degradation pathways were proposed. Two MB degradation pathways were observed (Figure 11b). The first involved the pathway, where the MB molecule was attacked by eaq– and •H, resulting in the formation of the intermediates I1 (m/z = 306) and I2 (m/z = 284). For the second pathway, the production of I3 (m/z = 301) was attributed to the oxidation of •OH.52 I4 (m/z = 270) and I5 (m/z = 256) were produced by eliminating the methyl group by breaking the -N-(CH3)2 bond.53 I6 (m/z = 139) and I7 (m/z = 136) were the products of consecutive hydroxylation and ring rupture processes.54 I3 was continuously attacked by •OH to form I8 (m/z = 202). Following this, it was oxidized to obtain I9 (m/z = 158).55 These intermediates were the products under 2 kGy conditions and were further oxidized and mineralized to form CO2, H2O, NO3–, SO42–, and other low-molecular-weight organics under conditions of large irradiation doses.

Figure 11.

Figure 11

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Degradation (a) mechanism and (b) pathways of MB in the EBI&CN/CD3/Fe6 system.

Table 3. Degradation Products of MB Identified by LC-MS.

3.6.

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It is worth mentioning that the intermediates of MB in the EBI and EBI&CN/CD3/Fe6 system were compared and analyzed. The EBI&CN/CD3/Fe6 system produced fewer intermediates compared to the EBI system, which were all low-molecular-weight substances. It can be inferred that the EBI&CN/CD3/Fe6 system is more favorable to realize the decomposition of the organic dyes to produce small molecules. Thus, the system exhibits a great application value for the mineralization of organic matters.

4. Conclusions

The degradation mechanism of organic dyes using the EBI&CN/CD3/Fe6 system was systemically studied. The degradation and mineralization of organic dyes were significantly promoted by the addition of CN/CD3/Fe6. The homogeneous irradiation system was more beneficial to realize the degradation of organic dyes than the EBI system since both the Haber–Weiss reactions in the solution and the catalytic role of CDs are the contributing factors for the generation of •OH. There may be surface reactions in the heterogeneous irradiation system to further promote the generation of •OH. The removal efficiency of organic dyes was not significantly affected in the pH range of 3–11, and the CN/CD3/Fe6 composite broadened the pH applicability of Fenton oxidation reactions for organic dyes. Cyclic experiments were conducted to study MB degradation, and the results indicated that the CN/CD3/Fe6 composite exhibited good stability and reusability after five times of irradiation. Results from scavenging experiments revealed that •OH played the most crucial role during the MB degradation process. A total of nine intermediates produced in the EBI&CN/CD3/Fe6 system were detected using the LC-MS technique, and the possible MB degradation mechanism was proposed. MB could be degraded by the reactive species, which are produced by three reaction pathways (water radiolysis (I), solution reactions (II), or surface reactions (III)); based on the results, two pathways for the MB degradation were proposed. The results revealed that the EBI&CN/CD3/Fe6 system could be effectively used to treat wastewater containing organic dyes.

Acknowledgments

This work was supported by the National Natural Science Foundation of China (21707108 and 11875138), Fundamental Research Funds for the Central Universities (WUT: 2017IVA109 and WUT: 2018IVB044) and State Key Laboratory of Advanced Electromagnetic Engineering and Technology (Grant No. AEET 2022KF011). The authors would like to thank the Accelerator and Radiation Processing Research Division of Huazhong University of Science and Technology for its technical support.

Supporting Information Available

The Supporting Information is available free of charge at https://pubs.acs.org/doi/10.1021/acsomega.2c00512.

Author Contributions

§ W.L. and Q.Y. contributed equally to this work.

The authors declare no competing financial interest.

Supplementary Material

ao2c00512_si_001.pdf (126.5KB, pdf)

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