Removal of Boron from Water by Mg-Al-Ce Hydrotalcite Adsorption

ZHANG Wei, LIU Chen, CHEN Yuantao, WU Wangsuo

Removal of Boron from Water by Mg-Al-Ce Hydrotalcite Adsorption

ZHANG Wei1,2, LIU Chen2, CHEN Yuantao2, WU Wangsuo1

(1. School of Nuclear Science and Technology, Lanzhou University, Lanzhou 730000, China; 2. School of Chemistry and Chemical Engineering, Qinghai Normal University, Xining 810008, China)

Boron is an important micronutrient for plants, animals, and humans. However, high concentrations of boron are harmful to animals and plants. A magnesium-aluminum-cerium hydrotalcite (Mg-Al-Ce-HT) was successfully prepared by the co-precipitation method for boron removal. Different analyses were conducted to confirm the structure and characteristics of Mg-Al-Ce-HT. Adsorption efficiency of Mg-Al-Ce-HT was studied as a function of initial pH, amount of adsorbent, concentration of initial boric acid, and contact time. The pH of the solution had a negligible effect on boron sorption when pH was less than 8.0. However, the adsorption capacity decreased when the pH exceeded 8.0. The optimum amount of the adsorbent was 200 mg, and the maximum adsorption capacity was 32.52 mg·g–1. Boron removal reached equilibrium at 160 min. The thermodynamic parameters revealed that the adsorption was a non-spontaneous and endothermic process. The data fitted well with the Langmuir model, which indicated that the process involved monolayer adsorption.

boron removal; hydrotalcite; adsorption

Boron is an important micronutrient for plants, animals, and humans. However, high concentrations of boron are harmful to animals and plants[1]. While excessive boron reduces the yield of fruit and causes premature and extensive leaf damage in plants, it causes the dysfunction of the cardiovascular, nervous, digestive, and reproductive systems in humans and animals[2]. The average abundance of boron in the earth's crust is 10–5[3], and it is often found in seawater, groundwater, and industrial wastewater. The concentration of boron in seawater is 4–5 mg·L–1and can reach up to 119 mg L–1in seawater surrounding some active volcanoes and groundwater with geothermal activity[4]. Higher level of boron is typically detected in industrial wastewater, which is likely discharged into rivers or seawater. In 2011, the World Health Organization (WHO)[5]limited the maximum allowable concentration of boron in drinking water to less than 2.4 mg·L–1, and many countries set more stringent standards to adhere to the WHO-recommended limit. Considering the higher levels of boron contamination in water resources and the need to meet the regulatory requirements, the development of effective boron removal methods is critical. Currently, the methods available for boron removal from water mainly include adsorption[6], ion exchange[7], electrocoagulation[8], che-mical coagulation[9], reverse osmosis[10], and membrane separation[11].The solid-adsorbent-based fixed bed method has been proven superior to the various techniques em-ployed for boron adsorption because of its operational simplicity and high adsorption efficiency[12]. The common adsorbents available for boron removal include boron- selective resin[13], fly ash[14], industrial waste[15], natural materials[16], oxides and hydroxides[17],hydrotalcite[18],and metal-organic frameworks[19]. Among them, hydrotalcite (hydrotalcite) is an economical and simple adsorbent for boron removal.

In this work, we prepared Mg-Al-Ce-HT by co- pre-cipitationmethod and studied the effects of initial pH, adsorbent content, initial boric acid concentration, tem-perature, and contact time on the adsorption performance.

1 Experimental section

1.1 Sample preparation

All reagents were chemical reagent grade and used without further purification. The Mg-Al-Ce hydrotalcite was synthesized by the co-precipitation method. Mg(NO3)2?6H2O (25 mmol), Al(NO3)3?9H2O (1 mmol), and Ce(NO3)3?6H2O (4 mmol) were dissolved in 40 mL deionized water (Solution I). NaOH (3.47 g) and Na2CO3(0.35 g) were dissolved in 40 mL of deionized water (Solution II). The solution I was added into solution II with stable stirring and placed at room temperature for 6 h. The resulting precipitate was separated by centrifugation and washed several times with deionized water until the pH of the supernatant reached nearly 8.0. The sediment was dried in vacuum at 60 ℃ for 12 h. The dried product was calcined at 400 ℃ for 4 h.

1.2 Boron adsorption

In boron adsorption studies, the amount of Mg-Al-Ce- HT was added into 50 mL aqueous solution of 100 mg·L–1H3BO3. The mixture was placed in a conical flask and shaken in a temperature-controlled shaker for 12 h at 25 ℃. The adsorbent was filtered off and the boron concentration of the residual solution was tested by ICP-OES. In order to explore the impact of different factors, the amount of adsorbent, initial pH, initial concentration of boric acid, and contact time varied across different batch experiments. For the adsorption and thermodynamics study, Mg-Al-Ce-HT was added into a series of aqueous boric acid solutions at different temperatures (308, 313, and 323 K). The adsorbent was dispersed into these boron solutions with 200 mg. The mixtures were placed in 50 mL conical flasks and shaken in a temperature- controlled shaker for 12 h. Upon completion of the adsorption process, the adsorbents were filtered off and the boron concentration was analyzed by ICP-OES.

1.3 Data analysis

The boron adsorption was studied using batch experimentation method. The effects of adsorbent content, initial pH, initial concentration, and adsorption isotherm contact time, were investigated. The adsorption percentages () and adsorption capacity (s) were calculated with the following equations, using the experimental data of the boric acid concentration after adsorption.

Where0(mg·L–1) is the initial boric acid concentration;e(mg·L–1) is the equilibrium concentration of boric acid;(g) is the mass of the adsorbent;(mL) is the volume of the solution.

2 Results and discussion

2.1 Characterization

Fig. 1 shows the TG-DSC curve for the Mg-Al-Ce-HT precursor, which indicates a broad endothermic peak for Mg-Al-Ce and a calcination temperature from 300 ℃ to 400 ℃ with a corresponding mass loss in the TG curve. Meanwhile, the DSC curve shows a broad exothermic peak at 350 ℃, which corresponds to the dehydration of Mg-Al-Ce-HT to form the final hydrotalcite structure. The dehydration is attributed to the loss of bound water in Mg-Al-Ce-HT, leading to the change in the material’s structure and the formation of the hydrotalcite structure. At the temperature higher than 400 ℃, the structure tends to stabilize and do not change further. Therefore, 400 ℃is considered as the optimum calcination temperature for Mg-Al-Ce-HT, and the material is used for all subsequent experiments.

Fig. 1 TG-DSC curveof Mg-Al-Ce-HT precursor

To compare the adsorption performances of the materials and confirm their structures, we conducted XRD analyses of the materials before calcination (Mg-Al-Ce-HT precursor), before (Mg-Al-Ce-HT) and after (adsorbed Mg-Al-Ce-HT) adsorption. The XRD patterns of Mg-Al-Ce-HT precursor (a), Mg-Al-Ce-HT adsorbent (b), and adsorbed Mg-Al-Ce-HT material (c) are shown in Fig. 2. From the diffraction patterns, the (003), (006), (009), (018), (110), and (113) crystal planes are registered in (a) and (b) curves, and the results are in agreement with those in the literature [20], which confirms the formation of the hydrotalcite structure. Because Mg-Al-Ce precursor is the unheat-treated material, the free water and nitrate radical reduces the diffraction peak intensity. Upon calcination of material (b), the free water and nitrate radicals are removed, and the intensity of the diffraction peaks is strengthened. The diffraction patterns of the calcined material (b) indicate the characteristic diffraction peaks of metal oxides. The peaks at 2=28.68° and 47.68° (JCPDS 02-1306) correspond to cerium oxide, and those of aluminum oxide and magnesium oxide are observed at 2=33.20°, 56.50° (JCPDS 29-0063) and 2=38.14°, 62.08° (JCPDS 65-0467), respectively. In Fig. 2 (b), because of the calcination of the materials, a part of the material changed to metal oxide. Owing to the memory effects of hydrotalcite materials, the structure of the adsorbed material (c) resembles that before the calcination, and the crystal plane peaks are similar with those in the Fig. 2(a).

FT-IR spectra of Mg-Al-Ce-HT precursor (a), the Mg-Al-Ce-HT material (b), and the adsorbed Mg-Al-Ce-HT material (c) are shown in Fig. 3. Compared to these curves, the structure of this material was stabilized. In the 3400–3650 cm–1broad-band range, all curves display characteristic absorption bands, which are attributed to the stretching mode of the structural O–H groups in the metal hydroxide layer. At 1636.78 cm–1, the bending vibrations of the hydroxyl group O–H bonds are clearly observed. On the curves (a) and (c), a sharp peak locates at 3699.76 cm–1which corresponds to the dissociated O–H vibration of residual water. The bands in the curve (b) at 1384.64 and 1456.47 cm–1are attributed to the CO32–in the material. The metal-oxygen-metal stretching vibrations are found at 1048.12 cm–1. Owing to the weak interaction during adsorption, the peak corresponding to boron is not observed in thes spectra.

Scanning Electron Microscopy (SEM) images of Mg-Al-Ce-HT are shown in Fig. 4 (a) and indicate that Mg-Al-Ce-HT is composed of flaky shaped particles with irregular sizes (10–100 μm). Further, the samples does not have crystalline structures.

Energy Dispersive Spectroscopy (EDS) analysis of Mg-Al-Ce-HT is shown in Fig. 4. The sample (b) has the same morphology as those of Mg-Al-Ce-HT (a), and the Fig. 4(c-f) showed that the O, Mg, Ce, and Al atoms are well-distributed in the materials, respectively. The ratio of abundances of these elements is 27.20% : 1.17% : 3.51%, which is in agreement with the proportion used for the synthesis. Furthermore, the presence of several oxygen atoms in this material indicates that it exists as metal oxide or hydrate. Combined with the results of FT-IR analysis, it is proved that the oxygen in the materials exists in the form of hydroxyl groups. The hydroxyl group plays an important role in boron removal.

Fig. 2 XRD patterns of Mg-Al-Ce precursor (a), Mg-Al-Ce-HT before adsorption (b), and Mg-Al-Ce-HT after adsorption(c)

Fig. 3 FT-IR spectra of Mg-Al-Ce-HT precursor (a); Mg-Al-Ce-HT materials (b) and adsorbed materials (c)

Fig. 4 SEM images of Mg-Al-Ce-HT (a) and EDS analysis of Mg-Al-Ce-HT (b) and the corresponding EDS mappings of O (c), Mg (d), Ce (e), and Al (f) elements

In order to confirm the possible mechanism of boron removal in Mg-Al-Ce-HT, X-ray photoelectron spectroscopy (XPS) of Mg-Al-Ce samples was conducted, and the results are shown in Scheme 1 (b). From the patterns, the peaks for Mg 2p, Al 2p, Ce 3d, C 1s, and O 1s exist in the adsorbent. Furthermore, the pattern shows that the structure of the material is nearly unchanged in the adsorption process. In the materials subjected to adsorption, the boron peaks appear at 198 eV, which proves the successful adsorption of boron in these materials.

The strong XPS peaks of Mg 2p, Al 2p, and Ce 3d in Mg-Al-Ce-HT particles before and after the adsorption display in Fig. 5. The Mg 2p, Al 2p, and Ce 3d peaks appear at 48.7, 73.4, and 881.3 eV, respectively, which indicate that the structure of Mg-Al-Ce-HT is nearly unchanged after the adsorption process, and the results were in good agreement with the XRD and FT-IR analyses.

The C 1s and O 1s XPS spectra of Mg-Al-Ce-HT particles before and after adsorption are shown in Fig. 5. The strong peaks at 283.8 and 284.7 eV correspond to the C 1s spectrum and the carbon atoms of carbonate CO32–on the surface. The strong peaks at 528.5 eV correspond to the metal oxide (M–O), and the band energy of 529.7 and 531.2 eV represent the hydroxyl groups bonded to the metal (M–OH) and the oxygen of water (H2O), respectively. In contrast, the examination of the peaks before and after adsorption reveal that the CO32–disappears, and the amount of metal oxide increases, which suggests the participation of the –OH groups on the adsorbent surface in the boric acid adsorption.

Scheme 1 Schematic of the B(OH)3 adsorption process on the surface of Mg-Al-Ce-HT material(a), and XPS patterns of full elemental spectrogram (b)

With the hydration creating, when the pH of solution above 8.0, the –OH is massive produced and dispersed in the solution, and the H3BO3(B(OH)3) gradually changes into B(OH)4–in solution[21]. Because B(OH)4–and OH–are negatively charged, B(OH)4–exclude with OH–, OH–in materials are not easy to capture the boron, so the adsorption process is slow until adsorption equilibrium.

In short, the driving forces for the adsorption reaction mainly depend on the reaction of the boric acid with the hydroxyl produced by hydration of the metal ions. Upon hydration of the metal ions in water, the hydroxyl groups on the surface of the metal are released, and the boric acid reacts with the hydroxyl groups adsorbed on the metals. Due to the hydration reaction, the dissociated hydroxyls in the solution increase gradually, and then the boric acid reacts with the dissociated hydroxyls directly, leading to the inhibition of the adsorption of boric acid on the materials.

2.2 Effect of initial pH and mechanism of adsorption

The initial pH of boric acid considerably affects the adsorption behavior. In order to investigate the effect of initial pH on boron removal, we carried out experiments at different pH. The experimental conditions were the same as those for the adsorption experiment, but the initial pH was set in the 3.0–12.0 range. The equilibrium amounts of boron adsorbed onto the Mg-Al-Ce-HT are plotted in Fig. 6(a), which show that at the pH range of 3.0 to 8.0, the values ofsfor Mg-Al-Ce-HT are almost constant around 21 mg·g–1. At pH above 8.0,sdecreases with increasing pH, and at pH above 12.0, thesof the adsorbent drops to 2 mg·g–1. At the boron concentration below 216.68 mg·L–1, it often exists in the B(OH)3or B(OH)4–forms[22], and the B(OH)3would convert to B(OH)4–under alkaline conditions.

The relationship between the conversion of these two materials is shown in Fig. 6(b). With the increase of pH, the concentration of B(OH)3reduces and that of B(OH)4–increases. In this experiment, at the high initial pH, the B(OH)3in the solutions becomes B(OH)4–. Because the massive B(OH)4–restrains the adsorption process and reduces the adsorption capacity. Therefore, the boric acid species removed in the adsorption process existed in the B(OH)3form.

2.3 Effect of amount adsorbent

In order to investigate the effect of adsorbent content, a series of experiments were conducted. The experimental conditions were the same as those of the adsorption experiment, but the adsorbent dosage varied from 50 mg to 350 mg. The effect of adsorbent content is shown as Fig. 7, and the results show that the adsorption capacity decreases with the increase in the adsorbent content, and the adsorption percentages increase under the same condition. At the low adsorbent content, the amount of effective adsorption sites in the system is low, which causes the lower levels of adsorption percentages and the higher levels of adsorbent capacity. With the increase of the adsorbent content, the effective adsorption sites gradually increases, leading to the decrease of the adsorption capacity from 35 to 15 mg·g–1and the increase of the adsorption percentages from 30% to 90%. At 200 mg of the adsorbent capacity, the system reaches the adsorption equilibrium. Therefore, 200 mg is considered as the optimum adsorbent content for boric acid and was used for all subsequent experiments.

Fig. 6 Effect of initial pH on adsorption efficiency (a) and the relationship between the conversion of H3BO3 and B(OH)4– (b)

Fig. 7 Effect of adsorbents, adsorption percentages, and ad-sorption capacity

2.4 Effect of initial concentration

In order to investigate the effect of the initial concentration of boric acid on boron removal, we conducted experiments at different concentrations. The effect of initial boric acid concentrations was investigated from 20 to 200 mg·L–1at 298 K. As shown in Fig. 8(a), the amounts of boron adsorbed on Mg-Al-Ce-HT are significantly affected by the initial feed concentrations of boron. Further, the adsorbent content increases with the increase in the initial concentration and reaches the adsorption equilibrium at 140.00 mg·L–1, and the curve maintained balance with the increase of the initial boric acid concentration. The reasons for this phenomenon are as follows: At the initial low concentration of boric acid, the effect of the adsorption sites is excessive in the system. With the increase of the boric acid concentration, the fraction of concentration and adsorption sites increase, and the adsorption efficiency also increases. When the adsorbent reaches the adsorption saturation, the efficiency did not change further.

The maximum adsorption capacity is confirmed by Langmuir model fitting, and the result displays in Fig. 8(b). The fitting data reveals that the maximum ad-sorption capacity is 32.52 mg·g–1. The correlation coefficient of the fitting data is 0.9271, which is within the permitted range of errors.

2.5 Effect of contact time and sorption kinetics

The effect of the contact time was explored next, and different contact times between the adsorbent and boric acid solutions were examined, and the experimental curve is shown in Fig. 9. In the first 100 min, with the increase of the contact time, the adsorption capacity increases quickly. Then, the adsorption efficiency gradually weakenes, and at 160 min, the adsorption reaches the equilibrium, and the adsorption capacity increases slowly. The reason for this phenomenon is the particular ratio of the adsorbent and concentration of boric acid. At the beginning of the adsorption, a high concentration of boric acid is present in the solution, and the adsorbent concentration is also massive in the system. Therefore, the adsorption process is fast at the beginning, and with the increase in adsorption, the adsorption capacity gradually reaches saturation, and the adsorption speed gradually slowed down. When the adsorption reaches the equilibrium, the adsorption capacity remains unchanged with increasing contact time.

Fig. 8 Effect of initial concentration of boric acid (a) and the Langmuir model (b)

The contact time data is fitted by pseudo-first-order and pseudo-second-order adsorption kinetics models. The equations for these models are described as follows:

The results show that the pseudo-second-order correlation coefficient (2=0.9133) is higher than the pseudo-first-order correlation coefficient (2=0.7548). Therefore, the pseudo-second-order kinetics model is best fitted for the adsorption.

2.6 Effect of temperature and adsorption isotherms

The thermodynamic parameters for the adsorption of boron on Mg-Al-Ce-HT were calculated. The Gibbs free energy change (Δ, kJ?mol–1), enthalpy (Δ, kJ?mol–1), and entropy change (Δ, kJ?mol–1?K–1) were calculated according to the following equations:

Where(8.314 kJ?mol–1) is the universal gas constant;is the temperature of the experimental process in Kelvin;cis the distribution coefficient by the Henry model. The Δ, Δ, and Δcan be obtained using Van’s Hoff plot of lnc. 1/(Fig. 10). The data obtained for Δ, Δ, Δ, and the fitting-square are shown in Table 1. Owing to the positive value obtained for Δ, the adsorption process on Mg-Al-Ce-HT for the removal of boron is determined to be a non-spontaneous endothermic process. The Δin the thermodynamic parameters is positive, and the boron adsorption capacity increases with the increase in the temperature, which confirms that the adsorption is endothermic.

3 Conclusion

The Mg-Al-Ce-HT with high boric acid adsorption performance was successfully prepared. SEM and EDS analy-ses show the patterns of Mg-Al-Ce-HT and provide the distribution of Mg, Al, Ce, and O. The XPS results reveal that boron is fully adsorbed into the materials. We explored the effects of initial pH, initial boric acid concentration, temperature, and contact time on boron removal. At initial pH greater than 8.0, the adsorption capacity stabilize at the maximum value. The adsorption capacity decreases, and the adsorption percentages increases. The adjusted adsorbent content for boron removal is determined to be 200 mg. The initial concentration of boric acid is another key factor for efficient boron removal. As the initial concentration of boric acid increases, the adsorption capacity increases until the initial concentration reaches a certain extent, beyond which the adsorption capacity stabilizes. The optimal initial concentration of boric acid is 100.00 mg·g–1, and the adsorption reaches the equilibrium at 160 min. The results fit best the pseudo-second-order adsorption kinetics model for the adsorption process.

Fig. 10 Van’s Hoff plot of boron adsorption on Mg-Al-Ce-HT

Table 1 Thermodynamic parameters for boron adsorption on Mg-Al-Ce-HT

[1] TANAKA M, FUJIWARA T. Physiological roles and transport mechanisms of boron: perspectives from plants., 2008, 456(4): 671–677.

[2] BLEVINS D G, LUKASZEWSKI K M. Proposed physiologic functions of boron in plants pertinent to animal and human metabolism., 1994, 102(suppl 7): 31–33.

[3] DUYDU Y, AYDIN S, UNDEGER U,. Is boric acid toxic to reproduction in humans? assessment of the animal reproductive toxicity data and epidemiological study results.2016, 13(3): 324–329.

[4] GEFFEN N, SEMIAT R, EISEN M S,. Boron removal from water by complexation to polyol compounds., 2006, 286(1): 45–51.

[5] TüRKER O C, BARAN T. Evaluation and application of an innovative method based on various chitosan composites and Lemna gibba for boron removal from drinking water.2017, 166: 209–218.

[6] HARADA A, TAKAGI T, KATAOKA S,Boron adsorption mechanism on polyvinyl alcohol., 2011, 17(1): 171–178.

[7] KIR E, GURLER B, GULEC A. Boron removal from aqueous solution by using plasma-modified and unmodified anion-exchange membranes., 2011, 267(1): 114–117.

[8] SARI M A, CHELLAM S. Mechanisms of boron removal from hydraulic fracturing wastewater by aluminum electrocoagulation., 2015, 458: 103–111.

[9] ARIFFIN M, HASSAN A, HUI L S,Removal of boron from industrial wastewater by chitosanchemical precipitation., 2009, 17(8/9): 521–535.

[10] HUERTAS E, HERZBERG M, ORON G,Influence of biofouling on boron removal by nanofiltration and reverse osmosis membranes.2008, 318(1): 264–270.

[11] PING Q, ABU-REESH I M, HE Z. Boron removal from saline water by a microbial desalination cell integrated with donnan dialysis.2015, 376: 55–61.

[12] WAITE T D, DAVIS J A, PAYNE T E,Uranium(VI) adsorption to ferrihydrite: application of a surface complexation model.,1994, 58(24): 5465–5478.

[13] DARWISH N B, KOCHKODAN V, HILAL N. Boron removal from water with fractionized Amberlite IRA743 resin.,2015, 370: 1–6.

[14] POLOWCZYK I, ULATOWSKA J, KO?LECKI T,. Studies on removal of boron from aqueous solution by fly ash agglomerates.,2013, 310(3): 93–101.

[15] LI J, CAO P, NI P,. Enhanced boron removal from metallurgical grade silicon by the slag refining method with the addition of tin., 2016, 51(9): 1598–1603.

[16] WANI M A. Adsorption and desorption of boron as influenced by soil properties in temperate soils of lesser himalayas., 2015, 46(6): 683–698.

[17] KAMEDA T, OBA J, YOSHIOKA T. New treatment method for boron in aqueous solutions using Mg-Al layered double hydroxide: kinetics and equilibrium studies., 2015, 293: 54–63.

[18] AY A N, ZüMREOGLU-KARAN B, TEMEL A. Boron removal by hydrotalcite-like, carbonate-free Mg-Al-NO3-LDH and a rationale on the mechanism., 2007, 98(1): 1–5.

[19] LYU J, ZENG Z, ZHANG N,Pyrocatechol-modified resins for boron recovery from water: synthesis, adsorption and isotopic separation studies.,017, 112: 1–8.

[20] RODRIGUES E, PEREIRA P, MARTINS T,Novel rare earth (Ce and La) hydrotalcite like material: synthesis and characterization., 2012, 78(7): 195–198.

[21] THEISS F L, AYOKO G A, FROST R L. Removal of boron species by layered double hydroxides: a review., 2013, 402(14): B114–121.

[22] WANG B, GUO X, BAI P. Removal technology of boron dissolved in aqueous solutions – a review., 2014, 444(4): 338–344.

Mg-Al-Ce水滑石吸附去除水中的硼

張煒1,2, 劉晨2, 陳元濤2, 吳王鎖1

(1. 蘭州大學 核科學與技術學院, 蘭州 730000; 2. 青海師范大學 化學化工學院, 西寧 810008)

用共沉淀法成功制備了鎂鋁鈰水滑石(Mg-Al-Ce-HT), 采用不同分析手段對材料進行表征。通過靜態(tài)吸附實驗研究了Mg-Al-Ce-HT的吸附效率與初始pH、吸附劑劑量、初始硼酸濃度和接觸時間的關系。當pH小于8.0時, 溶液的pH對硼吸附幾乎沒有影響, 當pH超過8.0時, 吸附容量降低。吸附劑的最佳用量為200 mg, 最大吸附容量為32.52 mg·g–1。硼去除量在160 min內達到平衡。吸附等溫線表明吸附過程是一個非自發(fā)的吸熱過程。吸附數據與Langmuir模型擬合良好, 表明吸附是單層吸附。

除硼; 水滑石; 吸附

TQ174

A

1000-324X(2020)03-0337-08

10.15541/jim20190383

date:2019-07-24;

date: 2020-01-07

ZHANG Wei(1972-), female, PhD candidate. E-mail: zhangwei@qhnu.edu.cn

張煒(1972-), 女, 博士研究生，E-mail: zhangwei@qhnu.edu.cn

Corresponding author:WU Wangsuo, professor, E-mail: wuws@lzu.edu.cn

吳王鎖, 教授, E-mail: wuws@lzu.edu.cn