Energy Engineering

DOI: 10.32604/ee.2022.015504

ARTICLE

HCl-Induced Hg0 Transformation over CuMn2O4 Sorbent

Aijia Zhang, Yingju Yang, Jing Liu* and Junyan Ding

State Key Laboratory of Coal Combustion, School of Energy and Power Engineering, Huazhong University of Science and Technology, Wuhan, 430074, China
**Corresponding Author: Jing Liu. Email: liujing27@mail.hust.edu.cn
Received: 23 December 2020; Accepted: 21 May 2021

1  Introduction

Mercury is a toxic air pollutant with high volatility, and is harmful to human health and ecosystem [1–5]. Thermal power plant is considered to be a main source of gaseous anthropogenic mercury emissions in China [6–8]. The Minamata Convention on Mercury has officially come into force in August 2017 to restrict the global anthropogenic mercury emissions [9]. In order to meet the requirements of the Minamata Convention on Mercury, the mercury emission limit of thermal power plants in China will be set to 1 μg/m3 in 2030 [10]. Therefore, mercury emission control in thermal power plants becomes increasingly urgent.

To date, mercury emission control technologies of thermal power plants mainly include: sorbent injection [11–16], catalytic oxidation [17–20] and bromide addition [21–23]. The technical strategy of catalytic oxidation and bromide addition is to oxidize Hg0 into Hg2+, which is subsequently removed by the wet flue gas desulfurization equipment. However, Hg2+ may be reduced to Hg0 in the wet desulfurization solution [24], leading to the secondary mercury pollution [25]. Therefore, sorbent injection is considered as an effective mercury emission control technology [26,27]. Currently, bromine-modified activated carbon is the commercial mercury sorbent. However, there are some problems during the application of activated carbon [28], such as high price, adverse effects on the quality of fly ash as the cement raw material, and non-recyclable utilization. Therefore, it is necessary to develop the cost-effective and regenerable mercury sorbents.

Currently, copper-manganese spinel oxide has received more and more attention due to its unique structure and physical-chemical properties [29]. Copper-manganese oxide has been widely used in the field of catalysis, such as CO oxidation [30], water-gas shift reaction [31], and pollutant removal [32]. The excellent catalytic activity of copper-manganese oxide is closely related to the flexible valence states of Cu+/2+ and Mn2+/3+/4+ [33]. The valence state changes of copper and manganese cations easily lead to an electron-transfer environment [34], which is beneficial to the adsorption and oxidation of Hg0. Therefore, our previous work synthesized copper-manganese spinel-type oxide and used to remove Hg0 from simulated flue gas (4% O2 + 12% CO2 + N2) [35–37]. HCl usually exists in flue gas, and has a great influence on the mercury transformation [38]. However, to date, no relevant research has been reported to investigate the effects of HCl on Hg0 transformation over CuMn2O4 sorbent.

In this work, the thermogravimetric (TG) analysis, BET specific surface area, and pore size distribution were used to evaluate the thermal stability and textural properties of CuMn2O4 sorbent. The effect of HCl on Hg0 transformation over CuMn2O4 sorbent was systematically investigated. The related effect mechanism was clarified based on the temperature-programmed desorption (TPD) analysis. This study can provide a theoretical basis for the application of CuMn2O4 sorbent.

2  Experimental Methods

2.1 Sorbent Synthesis and Characterization

CuMn2O4 sorbent was synthesized by our previously proposed low-temperature sol-gel auto-combustion synthesis method [35]. The detailed synthesis procedure has been provided in our previous work [35]. The thermal stability of sorbent was evaluated on a thermogravimetric analyzer (TA SDT-Q600). The temperature was increased from 25 to 850°C in the air atmosphere at a heating rate of 10 °C/min. The flow rate of air was set as 100 mL/min. The textural properties (such as specific surface area and pore size distribution) were investigated on a N2 physical adsorption apparatus (ASAP2020, Micromeritics). Sorbents were degassed at 200°C for 2 h before the N2 adsorption experiments.

2.2 Hg0 Removal Experiments

The Hg0 removal experiments were carried out in a fixed-bed reactor system, including a gas feed subsystem, a Hg0 generation subsystem, a quartz reactor, and an online mercury analyzer (VM3000, Mercury Instruments, Germany). The simulated flue gas (including 4% O2, 12% CO2, 0–10 ppm HCl, and N2 as the balance gas) were fed into the quartz reactor. In order to avoid the interference of other gas components (such as NO, SO2, and H2O) in the study of the effect mechanism of HCl on Hg0 transformation, these gas components were not included in the simulated flue gas. The total flow rate of the simulated flue gas was 1 L/min. Stable Hg0 vapor was continuously generated from a mercury permeation tube, and was fed into the simulated flue gas by N2. Hg0 concentration in the flue gas was maintained at 90 μg/m3. 0.2 g of sorbent was mixed with 1.8 g of quartz sand to reduce the pressure drop of flue gas through the sorbent bed and to prevent pipeline blockage. The height of sorbent bed was 19 mm, and the gas hourly space velocity (GHSV) was 5 × 104 h−1. Before the flue gas entering the mercury analyzer, the acid gas HCl was removed by a 10% NaOH solution to prevent the HCl corrosion of mercury measurement instrument. The experimental details have been clearly described in our previous work [35].

3  Results and Discussion

3.1 Characterization Analysis

3.1.1 TGA Analysis

Thermogravimetric analysis was used to investigate the thermal stability of CuMn2O4 sorbent. The TG and DTG curves of CuMn2O4 spinel in air atmosphere are displayed in Fig. 1. It can be seen that the weight of sorbent decreases slightly when the temperature increases and the weight loss curve of CuMn2O4 is flat. As the temperature increased from 25 to 350°C (the maximum temperature of Hg0 removal experiments), the weight loss was 0.61%, as shown in Fig. 1a. A small weight loss of 0.17% was obtained when the temperature further increased from 350 to 850°C. Differential thermogravimetric (DTG) curve was used to calculate weight loss rates, as shown in Fig. 1b. CuMn2O4 sorbent showed three endothermic peaks at 498, 583 and 825°C. Moreover, two exothermic peaks were also observed at 527 and 628°C. The largest weight loss rate of CuMn2O4 (0.0084%/min) occurs at 583°C. Obviously, these results indicate that CuMn2O4 sorbent has a good thermal stability at high temperatures.

Figure 1: TG-DTG curves of CuMn2O4 sorbent: (a) TG curve and (b) DTG curve

3.1.2 BET Surface Area and Pore Size Distribution

The BET surface area and pore size distribution were measured to understand the textural properties of CuMn2O4 sorbent. The N2 adsorption-desorption isotherms and pore size distribution of CuMn2O4 sorbent is shown in Fig. 2. According to the physical adsorption isotherm classification proposed by the International Union of Pure and Applied Chemistry (IUPAC), the N2 adsorption-desorption isotherm of CuMn2O4 sorbent is the type IV curve (Fig. 2a). There is an obvious hysteresis loop in the relative pressure range of 0.60–0.95, which is the typical feature of mesopores. The pore size of CuMn2O4 sorbent is mainly distributed in the range of 5–50 nm, suggesting the existence of mesoporous structure. The BET surface area, average pore size, and pore volume are 29.33 m2/g, 24.85 nm, and 0.18 cm3/g, respectively. Pores with a size between 2–50 nm are defined as mesopores [39]. Therefore, CuMn2O4 sorbent is a mesoporous material, which is favorable for the mass transfer during Hg0 capture.

Figure 2: (a) N2 adsorption-desorption isotherms; (b) Pore size distribution of CuMn2O4 sorbent

3.2 Mercury Removal Performance

3.2.1 Removal Efficiency

The mercury removal efficiency of CuMn2O4 sorbent in the temperature range of 50–350°C is shown in Fig. 3. It can be seen that CuMn2O4 sorbent shows >95% Hg0 removal efficiency over the wide temperature range. The excellent Hg0 removal efficiency may be attributed to the high concentrations of surface Cu atom and chemisorption oxygen. The XPS analysis of our previous work [35] found that the surface Cu and Mn atoms exist in the form of flexible valence (Cu+, Cu2+, Mn2+, Mn3+, and Mn4+). A part of Cu+ cations occupied the tetrahedral position of CuMn2O4 spinel, and some Mn4+ cations were located at the octahedral position of CuMn2O4 spinel. Thus, the different valence states and position distributions of metal cations (Cu+, Cu2+, Mn2+, Mn3+ and Mn4+) leaded to lattice distortion of CuMn2O4 spinel, resulting in an electron-transfer environment which can accelerate Hg0 adsorption and oxidation over CuMn2O4 sorbent. Therefore, CuMn2O4 sorbent exhibits excellent Hg0 removal performance in a wide temperature window.

Figure 3: Hg0 removal efficiency of CuMn2O4 sorbent at 50–350°C [35]

3.2.2 Adsorption Kinetics

A mathematical model is an effective tool to predict the Hg0 adsorption capacity of sorbent and to evaluate the performance of sorbent for mercury removal under different operating conditions [9]. The mathematical model can provide a rational basis for describing and characterizing the effectiveness of sorbent injection for mercury removal. In addition, the mathematical model can provide theoretical guidance for the development of new sorbents and for the optimization of sorbent injection process. Therefore, it is necessary to study the adsorption kinetics of mercury on the sorbent surface.

In a fixed-bed reactor, as the flue gas flows through a constant-temperature sorbent bed, the differential mass conservation equation of mercury can be described as:

u∂C∂z+∂C∂t+1−εε∂q∂t=Dax∂2C∂z2(1)

where u represents the flow velocity of flue gas. C represents the Hg0 concentration in the flue gas. ɛ represents the porosity of sorbent bed. q represents the Hg0 adsorption capacity of sorbent. Dax represents the axial diffusion coefficient. z represents the axial coordinate. t represents time. The differential mass conservation equation is closely related to the constitutive equation of Hg0 adsorption rate on the sorbent.

It was reported that the axial diffusion of mercury can be ignored if the ratio of the sorbent bed diameter (dbed) to the sorbent particle diameter (dparticle) is greater than 35 and the ratio of the sorbent bed thickness (hbed) to the sorbent particle diameter is greater than 75 [27]. In this work, dbed/dparticle and hbed/dparticle are 120 and 253, respectively. In addition, the Hg0 removal experiments were conducted under the condition of a larger flue gas flow rate of 1000 mL/min. These indicated that Hg0 removal process of CuMn2O4 sorbent is controlled by reaction kinetics. The chemisorption mechanism is responsible for Hg0 adsorption over CuMn2O4 sorbent. The chemical adsorption reaction has been incorporated into the mathematical model (i.e., Langmuir isotherm equation) of adsorption kinetics. Therefore, the mass diffusion resistance of mercury in the sorbent particle and the external boundary layer can be ignored. The Langmuir isotherm equation can be used to describe the adsorption process of Hg0 on the CuMn2O4 surface:

dqdt=kaCin(qe−q)(2)

where ka represents the rate constant of Hg0 adsorption on the sorbent surface. Cin represents the stable Hg0 concentration in the flue gas at the inlet of the fixed bed reactor. qe represents the equilibrium Hg0 adsorption capacity of CuMn2O4 sorbent. q represents the Hg0 adsorption capacity at time t. Integrating Eq. (2), q can be expressed as:

q=qe(1−exp⁡(−kaCint))(3)

k1 is used to replace kaCin, Eq. (3) can be expressed as:

q=qe(1−exp⁡(−k1t))(4)

The increment of Hg0 adsorption amount on the sorbent surface within the time range of Δ t can be calculated by the following formula:

Δq=Qm(Cin−Cout(t))Δt(5)

where Q represents the flow rate of flue gas. m represents the weight of sorbent. Cout(t) represents the Hg0 concentration in the flue gas at the reactor outlet at time t. During the whole Hg0 adsorption experiment, Hg0 adsorption amount of sorbent can be expressed as:

q=∫mtQm(Cin−Cout(t))dt(6)

In this work, Hg0 adsorption experiments were conducted for 2 h. Therefore, the integration time of Eq. (6) is 2 h. Eq. (4) was used to fit the experimental data at 150°C, as shown in Fig. 4. The adsorption kinetic parameters of Eq. (3) can be obtained: qe = 4774.57 μg/g, ka = 9.81 × 10−7 m3/(μg ⋅ min). Therefore, CuMn2O4 sorbent has a higher Hg0 adsorption capacity. Hg0 adsorption kinetics on the CuMn2O4 surface can be expressed as:

q=4774.57(1−exp⁡(−9.81Cin⋅t×10−7))(7)

Figure 4: Model fitting and experimental data of Hg0 adsorption amount of CuMn2O4 sorbent at 150°C

In order to further assess the accuracy and reliability of the adsorption kinetic model, Eq. (7) was used to predict the experimental results under the conditions of different reaction temperature. The comparison between the prediction results and experimental results at the reaction temperatures of 50, 100, 200, 250, 300 and 350°C is shown in Fig. 5. It can be seen that model predictions are in good agreement with the experimental results. Therefore, the kinetic model can accurately predict the Hg0 adsorption amount of CuMn2O4 sorbent in a wide reaction temperature range.

Figure 5: Comparison of experimental data and model predictions at different reaction temperatures: (a) 50°C, (b) 100°C, (c) 200°C, (d) 250°C, (e) 300°C, and (f) 350°C

3.3 Effect of HCl

HCl is the most important component for Hg0 oxidation in flue gas [40]. Therefore, it is necessary to investigate the effect of HCl on Hg0 transformation over CuMn2O4 sorbent. 10 ppm HCl was added to the simulated flue gas, Hg0 removal efficiency of CuMn2O4 sorbent at different reaction temperatures is shown in Fig. 6. In general, HCl shows little effect on the Hg0 removal efficiency of CuMn2O4 sorbent. It is well known that HCl can promote Hg0 adsorption and oxidation in flue gas [41]. However, CuMn2O4 sorbent can show >95% Hg0 removal efficiency in the absence of HCl. Therefore, Hg0 removal efficiency of CuMn2O4 sorbent does not depend on the presence of HCl. Since CuMn2O4 sorbent shows excellent Hg0 capture capacity and its Hg0 removal efficiency does not depend on the presence of HCl, HCl has almost no effect on Hg0 removal by CuMn2O4 sorbent. The slightly inhibitory effect (∼1.2%) at 200°C and promotional effect (∼1.3%) at 300°C of Fig. 6 are attributed to the experimental error rather than the effects of HCl. Although HCl has little effect on Hg0 removal efficiency of CuMn2O4 sorbent, HCl may affect the mercury speciation on the CuMn2O4 surface.

To further explore the effect of HCl on the mercury speciation over the CuMn2O4 surface, TPD experiments were carried out to identify the mercury speciation. The TPD curves of the used CuMn2O4 sorbent after Hg0 removal experiments in the absence and presence of HCl are shown in Fig. 7. After Hg0 removal experiments in the absence of HCl, the used CuMn2O4 sorbent only showed a peak at 385°C (Fig. 7a). This peak is attributed to the decomposition of yellow HgO species [42].

Figure 6: Effect of HCl on Hg0 removal efficiency of CuMn2O4 in the temperature range of 50–350°C

Figure 7: Temperature-programmed desorption curves of the used CuMn2O4 sorbent after Hg0 removal experiments in the (a) absence and (b) presence of HCl

However, after Hg0 removal experiments in the presence of HCl, there are two peaks at 330°C and 470°C in the TPD curve of the used CuMn2O4 sorbent (Fig. 7b). The TPD peak at 330°C is attributed to the decomposition of red HgO species adsorbed on the sorbent surface. Yellow HgO and red HgO have different crystal structure, leading to the different decomposition temperature. The desorption peak at 470°C is ascribed to the decomposition of HgCl2O8⋅H2O species [42]. Therefore, mercury species adsorbed on the CuMn2O4 surface in the presence of HCl mainly exist in the forms of HgO and HgCl2O8⋅H2O.

XPS analysis was further applied to illustrate the effect of HCl on the Hg0 transformation on CuMn2O4 sorbent surface. It can be seen in Fig. 8 that the peak of Hg 4f XPS spectra is observed at 104.61 eV. This is characteristic of Hg 4f5/2 spin-orbit doublet of Hg2+. This suggests that Hg0 is chemisorbed and transformed into oxidized mercury species (Hg-Cl compounds) on CuMn2O4 sorbent surface. Therefore, it can be inferred that Hg-Cl compounds are formed on CuMn2O4 sorbent in the presence of HCl.

Figure 8: Hg 4f XPS spectra of used CuMn2O4 sorbent

The performance of CuMn2O4 sorbent depends on the surface chemistry reactions. The overall process of Hg0 adsorption on CuMn2O4 sorbent in the presence of HCl is controlled by three steps. Firstly, Hg0 is chemically adsorbed on CuMn2O4 sorbent surface. Then, HgO is formed through the oxidation reaction of Hg0(ads) with chemisorbed oxygen on CuMn2O4 sorbent surface. Finally, HCl reacts with the adsorbed HgO to form Hg-Cl compound (HgCl2O8⋅H2O) on CuMn2O4 surface. The adsorption mechanism of Hg0 transformation on CuMn2O4 sorbent in the presence of HCl can be described by the following three chemical reactions [43]:

Hg0+catalyst→Hg0(ads)(8)

Hg0(ads)+O(s)→HgO(ads)(9)

HgO(ads)+HCl+O(s)→HgCl2O8.H2O(s)(10)

The formation of HgCl2O8⋅H2O species is governed by Eq. (10). The area of HgCl2O8⋅H2O desorption peak is much larger than that of HgO desorption peak, indicating that HgCl2O8⋅H2O is the main mercury specie on the used CuMn2O4 sorbent surface. Based on the above TDP analysis, it can be found that the presence of HCl shows a larger effect on the mercury speciation over the CuMn2O4 sorbent surface.

4  Conclusions

Experiments were conducted to investigate the effect mechanism of HCl on Hg0 transformation over CuMn2O4 sorbent. CuMn2O4 sorbent is a mesoporous material, and has a good thermal stability at high temperatures during Hg0 removal. The mesopores are favorable for mass transfer during Hg0 capture. CuMn2O4 sorbent shows >95% Hg0 removal efficiency in the wide temperature range of 50–350°C. The excellent Hg0 removal performance of CuMn2O4 sorbent is closely associated with the electron-transfer environment caused by the mixed valence states of Cu and Mn cations. The equilibrium adsorption capacity and adsorption rate constant are 4774.57 μg/g and 9.81 × 10−7 m3/(μg⋅min), respectively. The developed kinetic model can well predict Hg0 adsorption over CuMn2O4 sorbent. The Hg0 removal performance of CuMn2O4 sorbent is independent on the presence of HCl. Mercury species adsorbed on the used CuMn2O4 sorbent in the presence of HCl mainly exist in the forms of HgO and HgCl2O8⋅H2O. HCl shows a larger effect on mercury speciation over CuMn2O4 sorbent.

Funding Statement: This work was supported by National Key R&D Program of China (2016YFB0600604), National Natural Science Foundation of China (52006083), and Fundamental Research Funds for the Central Universities (2019kfyRCPY021).

Conflicts of Interest: The authors declare that they have no conflicts of interest to report regarding the present study.

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