Removal of Mercury from Coal-Fired Flue Gas and Its Sulfur Tolerance Characteristics by Mn, Ce Modified γ-Al2O3 Catalyst

He, Zhong; Xie, Yating; Wang, Yuan; Xu, Jingjie; Hu, Jiangjun

doi:https://doi.org/10.1155/2020/8702745

Journal of Chemistry

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Abstract Introduction Experimental Results and Discussion Conclusions Data Availability Conflicts of Interest Acknowledgments References Copyright Related Articles

Research Article | Open Access

Volume 2020 | Article ID 8702745 | https://doi.org/10.1155/2020/8702745

Removal of Mercury from Coal-Fired Flue Gas and Its Sulfur Tolerance Characteristics by Mn, Ce Modified γ-Al₂O₃ Catalyst

Zhong He,¹Yating Xie,¹Yuan Wang,¹Jingjie Xu,¹and Jiangjun Hu¹

Academic Editor: Woojin Lee

Received03 Apr 2020

Revised12 Jun 2020

Accepted23 Jun 2020

Published03 Aug 2020

Abstract

Mercury pollution in the atmospheric environment is a matter of international concern. Mercury in coal-fired flue gas is the first human mercury emission source and has become the focus of national mercury pollution control. The catalytic performance of zerovalent mercury (Hg⁰) in coal-fired flue gas was studied by using manganese-cerium-aluminum oxide as catalyst. The effects of metal loading ratio, reaction temperature, calcination temperature, and O₂ and SO₂ concentration on the efficiency of Hg⁰ catalytic removal were investigated, and the Mn-Ce/γ-Al₂O₃ catalysts before and after the reaction were characterized by BET, SEM, XRD, and XPS to analyze the physicochemical properties of the samples. The results show that the mercury removal efficiency of the composite catalyst with Mn, Ce, and Al as the active component is higher than that of the single metal catalyst. The catalytic activity of Mn_0.1Ce_0.02Al is the best, the optimum reaction temperature is 150°C, the optimum calcination temperature is 400°C, and the O₂ concentration in the conventional flue gas condition satisfies the effective oxidation of Hg⁰; SO₂ in the flue gas can seriously inhibit the oxidation of Hg⁰.

1. Introduction

In China, the dominated energy structure is still coal currently [1]. Mercury emissions from coal-fired flue gas have become the largest source of mercury pollution [2]. Generally, mercury in flue gas takes on three kinds of forms: elemental mercury (Hg⁰), oxidized mercury (Hg²⁺), and particle-associated mercury (Hg^p) [3, 4]. However, Hg⁰ is hard to be captured by the wet desulphurization and particulate matter control devices owing to its high volatility and low solubility in water. Thus, it makes sense to study catalysts capable of effectively transforming Hg⁰ into easily captured Hg²⁺ [5, 6].

At present, the Hg⁰ removal is concentrated on the modification of adsorbents and the development of new catalysts. However, the conventional SCR catalysts are not effective enough for Hg⁰ oxidation in the absence of HCl [5, 7, 8]. In order to increase Hg⁰ oxidation efficiency, the presence of an oxidant is generally necessary for metal oxide catalysts. Previous researches have established that chlorine is the most effective oxidant for heterogeneous mercury oxidation together with O₂ and the chlorine is originated from the HCl content in flue gas via a Deacon reaction [8–10]. However, the chlorine content of Chinese raw coal (63–318 mg/kg) is much lower than that of US coal (628 mg/kg) [11].

Transition metal oxides have a lower cost than precious metals, and their catalytic oxidation of Hg⁰ has been extensively studied. Common catalyst active components include MnO₂, CuO, Co₃O₄, Fe₂O₃, CeO₂, and Cr₂O₃ [12–20]. There are many different kinds of manganese oxides and many redox reactions can use them as the electron acceptor. It is the most catalytic metal oxide in nature [21]. CeO₂ can promote the transformation of Hg⁰ into oxidized Mercury even under anaerobic conditions [22, 23]. CeO₂ is a better cocatalyst, which has a good effect on the dispersion of metal active components; it can also enhance the thermal stability of the catalyst and inhibit the sintering; at the same time, CeO₂ can be effectively stored by mutual conversion between different valence states. Oxygen is collected to improve its oxidation performance [14, 24]. CeO₂ mainly produces high activity, unstable oxygen vacancies, and bulk oxygen in the redox reaction through the mutual conversion of Ce³⁺/Ce⁴⁺ [25–28]. Therefore, in low oxygen or even no oxygen, CeO₂ can also effectively promote the conversion of elemental mercury to oxidized mercury [28–31].

In this study, γ-Al₂O₃ was used as a carrier to prepare Mn-Ce-Al composite catalyst, and the performance of catalytic oxidation of Hg⁰ was studied in the simulated flue gas. The effects of metal loading, calcination temperature, and reaction conditions (flue gas temperature, O₂, SO₂ concentration, etc.) on the catalytic Hg⁰ removal efficiency were investigated experimentally.

2. Experimental

2.1. Catalyst Synthesis

2.1.1. Preparation of γ-Al₂O₃

15 g of aluminum nitrate was dissolved in 100 ml of deionized water, the pH was adjusted to 10 with diluted ammonia water (volume ratio of 1 to 2), water bath for 30 minutes at 60°C, static precipitation for 2 days, filtration, drying at 105C for one night, after γ-Al₂O₃ was obtained by burning at 550°C for 1 h in an air atmosphere in a muffle furnace [32].

2.1.2. Preparation of Mn_xCe_yAl Catalyst

The obtained γ-Al₂O₃ was ground, rinsed, and dried at 90°C for 24 hours in an electric blast drying oven. Prepare a mixed solution of C₄H₆MnO₄·4H₂O(AR) and Ce(NO₃)₃·6H₂O(AR), then place the mixed solution on a stirrer, and slowly pour a solution containing a certain amount of γ-Al₂O₃ added dropwise with diluted aqueous ammonia to adjust the pH at 10. Precipitate the liquid for two hours at 60°C, collect the precipitate, wash with distilled water, dry overnight at 110°C, and then calcine it in air at 450°C for 4 hours. The granules were sieved with a 60–80 mesh sieve to obtain a composite catalyst of different loadings. The obtained catalyst was represented by Mn_xCe_yAl [33].

2.2. Catalytic Activity Test

As shown in Figure 1, the laboratory-scale fixed-bed system for the removal of Hg⁰ and NO is composed of a gas distribution system, a mercury permeation tube (Beijing, Mingnick Analytical Instrument Equipment Center), a catalytic reactor, a temperature control system, a mercury absorption device, and an exhaust gas purification device. The catalytic reactor is placed in a temperature-programmed tubular electric furnace, and the prepared catalyst is placed in a quartz glass tube (inner diameter 10 mm, length 1000 mm). The Na₂S solution is used to absorb the mercury vapor in the exhaust gas [34], and the NaOH solution is used to absorb the acid gas in the exhaust gas.

500 mg catalyst was placed in the apparatus (the prepared catalyst was fired at 573 K for 1 h to remove moisture and other impurities). The simulated flue gas composition includes SO₂, NO, O₂, and H₂O, and the carrier gas is N₂, and the mercury vapor is carried into the pipeline and the adsorption system by the carrier gas. The mercury permeate tube is oil-bathed at 333 K. The Hg⁰ concentration in the system was controlled at 55 ± 2 μg/m³. The gas flow rate through the reactor was 1000 mL/min (corresponding to a space velocity of 100,000 h⁻¹ under standard temperature and pressure conditions). The Hg⁰ concentration at the inlet and outlet of the reactor was obtained from an Hg⁰ analyzer (AFS-930, Beijing Titan Instruments Co., Ltd.) [34].

2.3. Catalyst Characterization

BET (Brunauer–Emmett–Teller) is the most commonly used method for determining the specific surface area with an ASAP2020 analyzer (Micromeritics Inc., USA) at liquid nitrogen temperature. It is based on the adsorption theory, assuming the multimolecular layer adsorption occurs, and the total adsorption amount of the gas is the sum of the adsorption amounts of the layers. X-ray diffraction (XRD) experiments were carried out using a D/MX-IIIA diffractometer (Rigaku, Japan) to characterize the species distribution of the catalyst, crystallinity, and dispersivity of the supported species. Scanning electron microscopy (SEM) experiments were performed using the JSM-5610LV scanning electron microscope to determine the morphology and surface structure of the catalyst. X-ray photoelectron spectra (XPS) were carried out on a Thermo ESCALAB 250Xi apparatus with a monochromatic Al Kα (hν = 1486.6 eV) as the excitation source, to investigate the elemental states on the surface of the samples. All the binding energies were calibrated by the C 1s line at 284.6 eV Wang et al. [35].

3. Results and Discussion

3.1. Characterization of Samples

3.1.1. BET and XRD

The BET characterization results for different metal loading catalysts were shown in Table 1. The pure γ-Al₂O₃ has a relatively high specific surface area. The BET has a slight increase and then begins to decrease after Mn loading. This may be due to the small amount of load that causes γ-Al₂O₃ to adsorb on some tiny particles, which are beneficial to increase the specific surface area of the catalyst. When the Mn loading increases to a certain extent, the specific surface area will decrease. This may be because the metal occupies part of the pore space of γ-Al₂O₃, thereby causing clogging of the pores and agglomeration of the catalyst particles.

After loading Ce, the specific surface area, pore volume, and pore size of the catalyst change similarly to the loading of Mn. This may be because the thermal stability of cerium oxide is stronger. During the preparation process, especially during calcination, between cerium and manganese, the interaction can inhibit the agglomeration of manganese oxide.

In order to better compare the crystal composition of Mn-Ce-Al with Mn-Al and Mn-Ce-Cu-Al, the BET of Mn_0.1 Ce_0.02Cu_0.03Al was also shown in Table 1. The XRD diffraction pattern of Mn_0.1 Al, Mn_0.1Ce_0.02Al, Mn_0.1Ce_0.02CuAl catalyst is shown in Figure 2. It can be seen from the figure that there are obvious γ-Al₂O₃ diffraction peaks at 36.3°, 46.4°, and 67.1°, and Mn_0.1Ce_0.02Al, Mn_0.1Ce_0.02CuAl catalysts have a diffraction peak of 28.5°, but none of the three catalysts. A corresponding diffraction peak of Mn oxide (Mn₂O₃, MnO₂, etc.) was detected. This result can be explained by the single layer distribution theory [36]. When the amount of the supported substance is within a certain range, the surface of the carrier exists in a single layer distribution state. When the range is exceeded, the supported material will appear in the form of particles, and the characteristic diffraction peak characterized by XRD will be more obvious. Therefore, the diffraction peak of MnO_x which did not appear indicates that MnO_x did not undergo significant agglomeration and was uniformly distributed on the surface of the catalyst. At the same time, we observed that the peak intensity of γ-Al₂O₃ weakened after loading the active material, which also showed that the loading of the active metal increased the dispersibility of the surface material of the catalyst.

3.1.2. SEM

The figure below shows the SEM morphology of different magnifications of γ-Al₂O₃ and Mn_0.1Ce_0.02Al catalysts. As shown in Figure 3, the pure γ-Al₂O₃ has an irregular crystal structure and a smooth surface. After loading Mn and Ce, the surface of the catalyst is covered with a layer of floc. The floc-like load is more conducive to increasing the contact area between the catalyst and the adsorbate, which has a certain promoting effect on the adsorption capacity of the catalyst.

3.1.3. XPS

The X-ray photoelectron spectroscopy analysis of Mn 2p before and after the mercury removal reaction of Mn-Ce/γ-Al₂O₃ catalyst through 1000 ppm SO₂ is shown in Figure 4(a). The characteristic peaks of Mn 2p are mainly Mn 2p3/2 and Mn 2p1/2, and the characteristic peaks of Mn 2p 3/2 can be fitted to three secondary peaks: Mn²⁺, Mn³⁺, and Mn⁴⁺, and (1) the peak around 644.5 eV is Mn⁴⁺. Characteristic peak, (2) the peak around 641.7 eV, is the characteristic peak of Mn³⁺ and (3) the peak around 641.4 eV is the characteristic peak of Mn²⁺ [37, 38]. It can be seen from the figure that the form of Mn in the Mn-Ce/γ-Al₂O₃ composite oxide prepared by the coprecipitation method is mainly MnO₂ and Mn₂O₃, and MnO₂ accounts for more. The high characteristic ratio of Mn⁴⁺ is favorable for the oxidation of Hg⁰ because Mn⁴⁺ has a stronger oxidation capacity than Mn³⁺ [39]. The good mercury removal ability of MnOx-CeOx/γ-Al₂O₃ composite oxide at low temperature is directly related to the high valence state of metal Mn.

(a)

(b)

After the mercury removal reaction, the ratio of Mn⁴⁺ characteristic peaks in Mn-Ce/γ-Al₂O₃ is low, and the characteristic peak of Mn²⁺ appears. This indicates that Mn-Ce/γ-Al₂O₃ has some Mn⁴⁺ in the catalytic oxidation of Hg⁰ reduced to Mn³⁺ and Mn²⁺.

As shown in Figure 4(a), we use u to represent the spin-orbital state of Ce 3d3/2 and to represent the spin-orbital state of Ce 3d5/2 [39]. The u/, u2/, and u3/ peak pair represents the 3d¹⁰4f⁰ electronic state of Ce⁴⁺, and the u1/ peak pair represents the 3d¹⁰4f¹ electronic state of Ce³⁺. Previous studies have shown that there is no u1/ peak belonging to Ce³⁺ in the XPS spectrum of pure CeO₂ [24]. The synergistic effect of the support and manganese oxide in the catalyst can gradually increase the peak intensity of Ce³⁺. The presence of Ce⁴⁺/Ce³⁺ redox electron pairs on the catalyst surface can produce unbalanced charges, electron holes, and unsaturated chemical bonds [40]. These factors can enrich the surface of the catalyst with more chemically adsorbed oxygen, which is beneficial to the process. The conversion cycle between Ce⁴⁺ and Ce³⁺, as well as the storage and release of oxygen on the surface of the composite oxide [41], thereby increases its ability to oxidize Hg⁰. At the same time, after the catalytic oxidation of Mn-Ce/γ-Al₂O₃, the value of Ce⁴⁺/Ce³⁺ decreased from 4.68 to 3.65. It can be concluded that, in the oxidation process of Hg⁰, CeO₂ participates in the reaction and some Ce⁴⁺ converted to Ce³⁺.

3.2. Determination of Mn and Ce Loading

The reaction results of MnO_x/Al₂O₃ catalysts with different loadings at N₂ + 5%O₂ and a reaction temperature of 150°C are shown in Figure 5(a). The Hg⁰ removal efficiency of pure γ-Al₂O₃ is only 8%, because it is mainly physical adsorption at this time. As the Mn loading increases, the Hg⁰ removal efficiency is significantly improved. When the Mn/Al molar ratio is only 0.06, the Hg⁰ removal efficiency increases to 40%, which shows that MnO_x and γ-Al₂O₃ have a chemical adsorption effect on the Hg⁰ removal. When the Mn/Al molar ratio is 0.018, 0.03, 0.065, 0.08, and 0.1, Hg⁰ removal efficiency gradually increases, corresponding to 65%, 73%, 78%, 80%, and 82%. However, when the Mn/Al molar ratio increases to 0.147, the Hg⁰ removal efficiency did not increase to a great extent. When the Mn/Al molar ratio was 0.251, the Hg⁰ removal efficiency even decreased. The excessive Mn doping will further block the pores and reduce the contact probability of Hg⁰ and the active site. Besides, as Mn content increased, the crystallinity of MnOx on the support was enhanced, which was adverse for its catalytic performance [42], resulting in a slight decrease of the Hg⁰ removal efficiency.

(a)

(b)

As shown in Figure 5(b), Mn remains the main active component of the adsorbent, but the doping of Ce can significantly increase the Hg⁰ removal efficiency. When the molar ratio of Ce and Al is only 0.02, Hg⁰ removal efficiency is closed to 93%. However, the Hg⁰ removal efficiency has no significant change by continuing to increase the content of Ce.

Compared with pure γ-Al₂O₃, the Hg⁰ removal efficiency may be increased for two reasons after loading the metal. First, CeO₂ can store or release oxygen atoms through the Ce⁴⁺/Ce³⁺ redox electron pair and then pass through a series of the chemical reaction showing a strong catalytic effect, and as an important auxiliary component, it can also improve its oxidizing ability. Second, the incorporation of cerium can increase the specific surface area of the adsorbent, thereby increasing the mercury adsorption capacity of the adsorbent under low-temperature conditions, but excessive loading can cause clogging of the micropores, thereby reducing the physical and chemical adsorption capacity.

3.3. Effect of Calcination Temperature

During the preparation of the catalyst, the calcination temperature has an important influence on its activity. The mercury oxidation performance of the Ce_0.02Mn_0.1Al catalyst is shown in Figure 6, the calcination temperature was 100, 200, 300, 400, 500, 600, 700, and 800°C, N₂ + 5%O₂ flue gas condition, and the reaction temperature of mercury removal was 150°C. As the calcination temperature increases, the catalytic oxidation ability of the catalyst to mercury first increases and then decreases. When the catalyst was calcined at 100 to 400°C, the mercury removal efficiency increased. However, when the catalyst was calcined at 400 to 800°C, the mercury removal efficiency decreased rapidly, especially at high temperatures. The calcination temperature may affect the pore structure and surface crystal structure of the catalyst. The load component cannot be completely decomposed and converted into an active component at the low calcination temperature, and the supported component will occupy the surface of the carrier, thereby reducing the adsorption performance of the carrier. When the temperature rises, the active site will increase, and the oxidation efficiency will increase. However, when the temperature is higher than a certain value, the structure of the catalyst will be destroyed, and some active sites will be covered. At the same time, high temperature will make the active component sintered and the catalyst activity lowered. The optimal calcination temperature was 400°C, and the calcination temperature of the subsequent experimental catalyst was prepared at 400°C.

3.4. Effect of Reaction Temperature

To study the catalytic activity of the catalyst under low-temperature conditions, the Hg⁰ removal rate in the range of 50°C to 250°C was conducted under the condition of N₂+5%O₂ flue gas using Ce_0.02Mn_0.1Al catalyst. The results are shown in Figure 7.

It can be seen from the figure that the Hg⁰ removal rate increases first and then decreases with the increase of temperature. When the reaction temperature is lower than 150°C, the removal efficiency of mercury increases with the increase of temperature, and the reaction temperature is higher than 150°C. The mercury removal efficiency decreases with increasing temperature. High activity is maintained between 100 and −200°C.

It has been revealed that Hg⁰ oxidation over Mn-based catalyst follows the Mars–Maessen mechanism [42]. Hg⁰ must adsorb onto the catalyst first and then be oxidized by the surface lattice oxygen to form HgO. Apparently, high temperature is not conducive to the effective physical adsorption of Hg⁰ by the catalyst, resulting in lower Hg⁰ removal efficiency. Low temperature was proper for the catalyst to remove Hg⁰ [43, 44].

3.5. Effect of O₂

Figure 8 shows the change of Hg⁰ removal efficiency under different O₂ concentration conditions of Ce_0.02Mn_0.1Al type catalyst under N₂ as carrier gas and temperature of 150°C. It can be seen from the figure that O₂ plays an important role in the oxidation of Hg⁰. When O₂ concentration increases from 0 to 5%, Hg⁰ removal efficiency increases from 50% to 92%. When the O₂ concentration increases, the Hg⁰ removal efficiency will be slight and decline. It is known that the O₂ concentration in the flue gas is about 4.5%. Therefore, the O₂ concentration under the conventional coal-fired flue gas condition can satisfy the effective oxidation of Hg⁰.

3.6. Effect of SO₂

The SO₂ in the flue gas has a great influence on the activity of the catalyst, which may cause the passivation of the catalyst to be deactivated [45, 46]. The catalyst is intended to catalyze the oxidation of Hg⁰ before the desulphurization system. Therefore, it is necessary to study the mercury removal performance of the catalyst under a high concentration of SO₂. Figure 9 shows the Hg⁰ removal rate at a temperature of 150°C under a condition of N₂ + 5% O₂ flue gas using a Ce_0.02 Mn _0.1 Al type catalyst.

It can be seen from the figure that, with the increase of SO₂ concentration, the mercury removal efficiency gradually decreases. When the SO₂ concentration is 2000 ppm, the mercury removal rate is only 50%, which indicates that the presence of SO₂ will greatly inhibit the catalytic oxidation of Hg⁰. This may be due to the competitive adsorption of SO₂ and Hg⁰ on the surface of the catalyst under N₂ conditions; that is, SO₂ reacts with the active oxygen on the surface of the catalyst to form SO₃ [6], thereby reducing the reaction rate of Hg⁰ with the surface active oxygen of the catalyst. In addition, SO₂ may react with MnO_x to form a stable MnSO₄, covering the surface of the catalyst, causing poisoning of the catalyst.

3.7. Mechanism

Through the above reaction results and characterization, the catalytic oxidation of Mn-Ce/γ-Al₂O₃ to mercury in the absence of HCl can be explained by the Mars–Maessen mechanism [21]. The following are specific reactions:

To verify the above conjecture, experiments on the change of mercury removal efficiency of MnO_x-CeO_x/γ-Al₂O₃ at different temperatures and different times under anaerobic and aerobic conditions were carried out. It can be seen from Figure 10 that, under pure N₂ conditions, the oxidative removal efficiency of mercury is up to about 48%, while the γ-Al₂O₃ with a higher specific surface area is only 25% under the same conditions, which indicates that, under anaerobic conditions, lattice oxygen may participate in the reaction. When 5% O₂ was added to N₂, the mercury removal efficiency was improved as a whole. When the reaction was carried out at 150°C for 140 min, the mercury oxidative removal efficiency reached 93%, indicating that the newly added O₂ promoted the lattice oxygen to continue to function. Thereby, more Hg⁰ is oxidized.

Meanwhile, as shown in Figure 10, when the reaction temperature is increased to 200°C, even if the reaction time is increased, the mercury oxidative removal efficiency is lowered, which indicates that Hg⁰ formed on the catalyst is released or unstable due to higher temperature.

4. Conclusions

γ-Al₂O₃ supports the active components Mn and Ce, which greatly improves the catalytic oxidation performance of Hg⁰. The catalyst (molar ratio) of Mn_0.1Ce_0.02Al has the best activity, and the optimum calcination temperature for the preparation of the catalyst is 400°C. The optimal activity temperature ranges of the Mn-Ce/γ-Al₂O₃ catalyst are 100–200°C. Under the condition of lower reaction temperature, Hg⁰ can be effectively removed, and the Hg⁰ emission standard is increasingly strict. It is a simple and effective means of mercury removal. The SO₂ in the flue gas forms competitive adsorption on the catalyst, which leads to a decrease in the efficiency of the Hg⁰ oxidation reaction at the active site and inhibits the mercury removal activity of the catalyst.

Data Availability

The data used to support the findings of this study are included within the article.

Conflicts of Interest

The authors declare that they have no conflicts of interest.

Acknowledgments

The authors would like to thank Test Center of Wuhan University for the support.

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Copyright © 2020 Zhong He et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

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