Solidiﬁcation/Stabilization of MSWI Fly Ash Using a Novel Metallurgical Slag-Based Cementitious Material

: Four industrial wastes, i.e., blast furnace slag, steel slag, desulfurization ash, and phosphoric acid sludge, were used to prepare a low-carbon binder, metallurgical slag-based cementitious material (MSCM). The feasibility of solidiﬁcation/stabilization of municipal solid waste incineration (MSWI) ﬂy ashes by MSCM were evaluated, and the immobilization mechanisms of heavy metals were proposed. The MSCM paste achieved 28-day strength of 35.2 MPa, showing its high-hydration reactivity. While the ﬂy ash content was as high as 80 wt.%, the 28-day strength of MSCM-ﬂy ash blocks reached 2.2 MPa, and the leaching concentrations of Pb, Zn, Cr, and Hg were much lower than the limit values of the Chinese landﬁll standard (GB 16889-2008). The immobilization rates of each heavy metal reached 98.75–99.99%, while four kinds of MSWI ﬂy ashes were solidiﬁed by MSWI at ﬂy ash content of 60 wt.%. The 28-day strength of binder-ﬂy ash blocks had an increase of 104.92–127.96% by using MSCM to replace ordinary Portland cement (OPC). Correspondingly, the lower leachability of heavy metals was achieved by using MSCM compared to OPC. The mechanisms of solidiﬁcation/stabilization treatment of MSWI ﬂy ash by MSCM were investigated by XRD, SEM, and TG-DSC. Numerous hydrates, such as calcium silicate hydrate (C-S-H), ettringite (AFt), and Friedel’s salt, were observed in hardened MSCM-ﬂy ash pastes. Heavy metals from both MSWI ﬂy ash and MSCM could be effectively immobilized via adsorption, cation exchange, precipitation, and physical encapsulation.


Introduction
The incineration of municipal solid wastes can remarkably reduce the volume of wastes, save a large amount of land for landfill disposal, as well as recover energy to generate electric power. Thus, it has become the most widely adopted method in China to dispose municipal solid wastes. In the years of 2011-2020, the number of municipal solid waste incineration (MSWI) plants in China rose by 303%, and the incineration capacity increased from 32,485 to 124,076 kilotons, accounting for 51.2% of treated municipal solid wastes in 2020 [1]. However, the incineration of municipal solid wastes produces secondary solid residues, including MSWI fly ash with high contents of toxic heavy metals [2][3][4]. MSWI fly ash, classified as hazardous waste in many countries, must be carefully disposed to meet certain standards before its landfill, owing to the severe negative impact on the environment and human health [4,5].
The cement-based solidification/stabilization is a typical process to immobilize toxic heavy metals in MSWI fly ashes [6][7][8]. The ordinary Portland cement (OPC) is a widely

Materials
The blast furnace slag (BFS), steel slag (SS), and desulfurization ash (DA) were collected from Wuhan Metal Resources Company in Hubei Province, China. The phosphoric acid sludge (PAS) was provided by China City Environment Protection Engineering Limited Company. The received BFS, with a specific surface area of 530 m 2 /kg, was directly used without further treatment. The granular SS, with a particle size of <10 mm, was ground to be a specific surface area of 550 m 2 /kg using a ball mill (SM500 × 500). The DA, with a specific surface area of 573 m 2 /kg, was dried at 105 • C for 4 h. The PAS with high water content was firstly dried at 105 • C for 10 h, then ground to be a specific surface area of 520 m 2 /kg. The OPC used was 32.5 # ordinary Portland cement. Four kinds of MSWI fly Minerals 2022, 12, 599 3 of 15 ashes were collected from MSWI plants in Wuhan, Baoding, Beijing, and Tangshan cities in China and were nominated as FA1, FA2, FA3, and FA4 in this study, respectively.
The chemical compositions and heavy metal contents of raw materials to prepare MSCM are given in Table 1, respectively. The XRD patterns of raw materials are shown in Figure S1. The main crystalline phases of DA were calcite, anhydrite, and calcium sulfite. Typical crystalline lines of gypsum (CaSO 4 ·2H 2 O) were not observed. The PAS contained calcite and calcium sodium phosphate as the main crystalline phases. As shown in Table 1, the P 2 O 5 content of PAS reached 21.76 wt.%, indicating that soluble phosphorous salts can immobilize heavy metals by forming insoluble metal phosphates [24]. As given in Table 1, the contents of CaO, SiO 2, and Al 2 O 3 in raw materials to prepare MSCM were high, contributing to the formation of hydration products. Heavy metal (Zn, Cr, Pb and Hg) contents were very low for BFS and PAS. However, as shown in Table 1, the DA had high contents of Pb and Zn, and the Cr content was also high in SS. The results indicated that toxic Pb, Zn, and Cr elements from prepared MSCM would be incorporated into MSCM-fly ash blocks. Thus, heavy metals from both MSCM and MSWI fly ash should be considered together to evaluate the immobilization rates of heavy metals.

Preparation of Binder-MSWI Fly Ash Blocks
The MSCM was produced by optimizing the mass ratio of PAS:SS:DA:BFS at 20 wt.%:32 wt.%:12 wt.%:36 wt.% with the results given in Table S1 At this mass ratio, pure MSCM paste achieved the highest hydration reactivity owing to the highest 28-day comprehensive strength. The MSCM-fly ash pastes were prepared by mixing the proportional fly ash and MSCM. Then, the water was added into the mixtures at water to solid ratios (w/s) of 0.35~0.55 to achieve similar flowability of different MSCM-fly ash pastes. After the mixing, the pastes were casted into steel molds (30 mm × 30 mm × 30 mm), and demolded after 24 h. The samples were cured at 20 ºC and relative humidity of 90% in a standard curing box for three, seven, and twenty-eight days. The compressive strengths of the samples were measured according to the Chinese national standard, "Test method for strength of cement mortar" (GB/T 17671-1999). Three samples were tested to obtain the average value.
To investigate the effect of fly ash contents, eight groups of MSCM-fly ash blocks (D1, D2, D3, D4, D5, D6, D7, and D8) were prepared by using FA2 as typical MSWI fly ash at the mass proportions of 10 wt.%, 20 wt.%, 30 wt.%, 40 wt.%, 50 wt.%, 60 wt.%, 70 wt.%, and 80 wt.%, respectively. For comparative purposes, pure MSCM paste (0 wt.% of fly ash) was also prepared and assigned as the D0 sample in this study. To study the solidification/stabilization of different MSWI fly ashes by the MSCM, the mass proportions of fly ash were set at 40 wt.% and 60 wt.%, respectively, as given in Table 2. Additionally, the solidification/stabilization of FA1 was compared using MSCM and OPC as the binders, respectively. Two pastes, D0 (100 wt.% MSCM + 0 wt.% FA2) and D4 (60 wt.% MSCM + 40 wt.% FA2), were used to investigate the immobilization mechanisms of heavy metals. In this work, the proportions of binders and MSWI fly ash to prepare different fly ash blocks are summarized in Table 2. After the specified curing period, the crushed blocks were put into anhydrous ethanol to stop the hydration reactions. The powers were collected and dried at 50 • C overnight for leaching tests and characterization measurements.

Leaching Tests and the Characterization
According to the "Solid waste leaching toxicity method-acetic acid buffer leaching method" (HJ/300-2007), the acetic acid buffer method was conducted to leach heavy metals from as-received MSWI fly ashes and cured block samples. Dried block samples were first crushed to below 3 mm before the leaching tests. Samples of 100 g were mixed with buffered acetic acid (pH of 2.64) at a liquid to solid ratio of 20 L/kg. Then, the mixtures were tumbled using an end-over rotator for 18 h at a speed of 30 rpm. After the leaching, 10 mL of the extract was extracted and further filtered through 0.45 µm glass fiber filter. The concentrations of heavy metals in the filtrated leachate were determined using inductively coupled plasma-mass spectrometers (ICP-MS, Shimadzu 2030, Shimadzu Corporation, Kyoto, Japan). The heavy metal immobilization rate in the binder-fly ash blocks was calculated as follows: where, S was the immobilization rate of the heavy metal; C 0 was the heavy metal concentration in the leachate (mg/L); L was the volume of the leachate (L); M was the mass of the dried samples for the leaching test (kg); γ i was the mass proportion of PAS, SS, DA, BFS, and fly ash in the block (%); β i was the heavy metal content in PAS, SS, DA, BFS, and fly ash (mg/kg). Thus, the incorporation of heavy metals in raw materials for preparing MSCM into the blocks was fully considered to calculate the immobilization rates of heavy metals. The X-ray powder diffraction (XRD) patterns of the samples were recorded by an X-ray diffractometer (D/Max-RC, Rigaku, Tokyo, Japan) with a Cu Kα radiation at a scanning speed of 0.04 • /s and a diffraction angle of 5~80 • . The thermogravimetric analysis (TGA, Rigaku Thermo plus, Tokyo, Japan) was performed on approximately 10 mg of crushed MSCM-fly ash blocks to determine the decomposition of the phases at high temperatures. The morphology and microstructures of cured pastes were observed by a field emission scanning electron microscope (SEM, Carl Zeiss, Oberkochen, Germany).

Characterization of MSWI Fly Ashes
The chemical compositions and XRD pattens of four MSWI fly ashes are given in Table S2 and Figure 1, respectively. All of four fly ashes had high contents of CaO, indicating the presence of reactive portlandite and lime. Except for the FA4, the other three fly ashes had high contents of Cl, Na 2 O, and K 2 O. The result was consistent with the presence of chloride salts (NaCl, KCl and CaClOH), as confirmed by XRD analysis. The mineral phases of FA4, mainly existing as quartz and calcium silicate, were quite different from FA1, FA2, and FA3.
ning speed of 0.04 °/s and a diffraction angle of 5~80°. The thermogravimetric analysis (TGA, Rigaku Thermo plus, Tokyo, Japan) was performed on approximately 10 mg of crushed MSCM-fly ash blocks to determine the decomposition of the phases at high temperatures. The morphology and microstructures of cured pastes were observed by a field emission scanning electron microscope (SEM, Carl Zeiss, Oberkochen, Germany).

Characterization of MSWI Fly Ashes
The chemical compositions and XRD pattens of four MSWI fly ashes are given in Table S2 and Figure 1, respectively. All of four fly ashes had high contents of CaO, indicating the presence of reactive portlandite and lime. Except for the FA4, the other three fly ashes had high contents of Cl, Na2O, and K2O. The result was consistent with the presence of chloride salts (NaCl, KCl and CaClOH), as confirmed by XRD analysis. The mineral phases of FA4, mainly existing as quartz and calcium silicate, were quite different from FA1, FA2, and FA3. The heavy metal contents and corresponding leaching concentrations of the received MSWI fly ashes are given in Table 3. It can be seen from Table 3 that both contents and leachability of heavy metals in four MSWI fly ashes were quite different from each other. Generally, the Pb and Zn had high contents in all MSWI fly ashes. In particular, the Pbleaching concentration of FA1 and FA2 reached 46,400 and 8160 μg/L, respectively, which The heavy metal contents and corresponding leaching concentrations of the received MSWI fly ashes are given in Table 3. It can be seen from Table 3 that both contents and leachability of heavy metals in four MSWI fly ashes were quite different from each other. Generally, the Pb and Zn had high contents in all MSWI fly ashes. In particular, the Pbleaching concentration of FA1 and FA2 reached 46,400 and 8160 µg/L, respectively, which were much higher than the permitted level (250 µg/L) of the Chinese standard for pollution control on landfill sites of municipal solid waste (GB 16889-2008). Additionally, the FA1 and FA4 had high Zn-leaching concentrations of 5080 and 11,100 µg/L, respectively. Therefore, it was essential to control environmental hazards of MSWI fly ashes prior to the landfilling. In this study, it was found that the chemical compositions, mineral phases, and heavy metal leachability were quite different for four kinds of MSWI fly ashes. Thus, it was quite necessary to evaluate the solidification/stabilization performance of different MSWI fly ashes by MSCM.

Solidification of MSWI Fly Ash with Different Proportions
In this work, the MSWI fly ash (FA2), collected from Baoding City, Hebei Province, China, was selected to investigate the effect of fly ash contents on solidification/stabilization performances of MSCM-fly ash blocks. For comparative purposes, the strength and heavy metal leaching concentrations of hardened MSCM pastes were also measured. As shown in Figure

Solidification of MSWI Fly Ash with Different Proportions
In this work, the MSWI fly ash (FA2), collected from Baoding City, Hebei Provi China, was selected to investigate the effect of fly ash contents on solidification/stabil tion performances of MSCM-fly ash blocks. For comparative purposes, the strength heavy metal leaching concentrations of hardened MSCM pastes were also measured shown in Figure 2, the compressive strength of MSCM pastes had reached 26.9 and MPa after curing for 3 and 28 days, respectively. In particular, the three-day stren reached 76.42% of 28-day strength, demonstrating the fast early-strength developmen MSCM pastes. It indicated that the MSCM, prepared from four industrial wastes (BFS DA, and PAS), achieved high cementitious reactivity.
As exhibited in Figure 2, the 28-day compressive strength of MSCM-fly ash blo decreased rapidly from 34.1 to 2.2 MPa as the FA2 content rose from 10 wt.% to 80 w Rémond et al. [25] also concluded that the mechanical strength of OPC-fly ash pa would reduce significantly as the MSWI fly ash content exceeded 15 wt.%. In this case 28-day strength of the blocks could reach 2.2 MPa, while the FA2 content was as hig 80 wt.%. It was worth noting that the mechanical strength of MSCM-fly ash blocks co well meet the strength requirements of sanitary landfills (~2.0 MPa).  As exhibited in Figure 2, the 28-day compressive strength of MSCM-fly ash blocks decreased rapidly from 34.1 to 2.2 MPa as the FA2 content rose from 10 wt.% to 80 wt.%. Rémond et al. [25] also concluded that the mechanical strength of OPC-fly ash pastes would reduce significantly as the MSWI fly ash content exceeded 15 wt.%. In this case, the 28-day strength of the blocks could reach 2.2 MPa, while the FA2 content was as high as 80 wt.%. It was worth noting that the mechanical strength of MSCM-fly ash blocks could well meet the strength requirements of sanitary landfills (~2.0 MPa). Figure 3 showed the leaching concentrations of Zn, Cr, Hg, and Pb in MSCM-fly ash blocks at different FA2 contents and curing times. As shown in Figure 3, hardened MSCM pastes (0 wt.% FA2) had very low-leaching concentrations of Zn, Cr, Hg, and Pb. The immobilization rates of Zn, Cr, Hg, and Pb for the D0 sample (MSCM paste) were above 99.60%, as given in Table 4. As listed in Table 1 decreased from 8160 and 144 μg/L for the original FA2 to 148 and 4.9 μg/L for FA2 blocks, respectively, with the addition of 20 wt.% MSCM. The results indicated that the solidification/stabilization of MSWI fly ash by the MSCM could comply well with the landfill site requirements. As listed in Table 4, the immobilization rates of Zn, Cr, Hg, and Pb were above 99.70%, while the FA2 content was 80 wt.%. It seemed that almost 100% of heavy metals from both MSWI fly ash and MSCM had been immobilized into solidified blocks. Based on the above results of strength and heavy metal leachability, it can be concluded that novel MSCM was a cost-effective, low-carbon, and highly efficient cementitious material for the solidification/stabilization treatment of MSWI fly ash.   As exhibited in Figure 3, while the FA2 content even reached 80 wt.%, the leaching concentrations of Zn, Cr, Hg, and Pb in MSCM-fly ash blocks were far below limit values of the Chinese landfill standard (GB 16889-2008).The Pb and Cr concentrations especially decreased from 8160 and 144 µg/L for the original FA2 to 148 and 4.9 µg/L for FA2 blocks, respectively, with the addition of 20 wt.% MSCM. The results indicated that the solidification/stabilization of MSWI fly ash by the MSCM could comply well with the landfill site requirements. As listed in Table 4, the immobilization rates of Zn, Cr, Hg, and Pb were above 99.70%, while the FA2 content was 80 wt.%. It seemed that almost 100% of heavy metals from both MSWI fly ash and MSCM had been immobilized into solidified blocks. Based on the above results of strength and heavy metal leachability, it can be concluded that novel MSCM was a cost-effective, low-carbon, and highly efficient cementitious material for the solidification/stabilization treatment of MSWI fly ash.
As shown in Figure 3, the leaching concentrations of Zn, Cr, and Pb decreased by extending the curing times. However, the Hg concentrations became higher after three days of curing treatment. It may be attributed to the degree of hydration reactions of MSCM-fly ash pastes. The leachability of heavy metals in fly ash blocks was highly related to alkalinity, the amount and type of hydrates, as well as the densification of the blocks [26]. The hydration reactions of BFS, SS, and DA in MSCM-fly ash pastes resulted in the generation of various hydrates, such as C-S-H gel, Aft, and Ca(OH) 2 . As the curing time was extended, the densification and alkalinity of the blocks should increase due to higher amounts of formed C-S-H gel and Ca(OH) 2 , immobilizing heavy metals by physical encapsulation and chemical precipitation [6,7]. Additionally, these hydrates can also immobilize heavy metals via multiple pathways, such as adsorption and cation exchange [6,10]. Thus, it was reasonably observed that more heavy metals (Zn, Cr, and Pd) were immobilized in the blocks at extended curing times.

Solidification of Four Kinds of MSWI Fly Ashes
In this work, the solidification/stabilization of four kinds of MSWI fly ashes was evaluated by using the MSCM as the binder. As listed in Table 5, the 28-day compressive strength of four kinds of fly ash blocks decreased from 16.4-24.1 MPa at 40 wt.% fly ash to 8.9-13.0 MPa at 60 wt.% fly ash. Nevertheless, the strength was still much higher than the strength requirements of sanitary landfills (~2.0 MPa). The decreased strength at higher fly ash contents may be partially attributed to the higher porosity of fly ash blocks [27]. As shown in Table 5, the H4-1 and H4-2 samples for the solidification/stabilization of FA4 achieved the higher strength compared to other fly ash blocks. It may be attributed to the lower content of Cl and higher contents of Al 2 O 3 and SiO 2 for the FA4, as seen in Table S2. According to the above results, it can be concluded that the hydration reactivities of MSWI fly ashes collected from four cities were quite different because of different chemical compositions and mineral phases. As given in Table 5, the leaching concentrations of Zn, Cr, Pb and Hg were just in the range of 1.17-25.64 µg/L for all MSCM-fly ash blocks, much lower than the limited values of the Chinese landfill standard (GB 16889-2008), as listed in Table 3. Taking the FA1 as an example, the leaching concentrations of Pb and Zn reached 46,400 and 5080 µg/L for original FA1, respectively. By solidifying FA1 with the addition of 40 wt.% MSCM (H1-2 sample), the Pb and Zn concentrations decreased significantly to only 25.64 and 3.31 µg/L, respectively. For all MSWI fly ashes, the immobilization rates of Zn, Cr, and Pb exceeded 99.90% and that of Hg reached above 98.70% at 60 wt.% fly ash. Based on the above results, it is suggested that the solidification/stabilization of MSWI fly ashes from different cities by using novel MSCM as a low-carbon binder could achieve high strength of fly ash blocks and low leachability of heavy metals.

Comparison of MSWI Fly Ash Solidification by MSCM and OPC
In this case, the solidification/stabilization treatment of FA1 by MSCM and OPC was compared. Due to high-leaching concentrations of Zn, Pb, and Hg, as seen in Table 3, the FA1 was selected as the typical MSWI fly ash for the comparison. For the solidification/stabilization treatment by OPC, the OF1 and OF2 samples represented OPC-fly ash blocks with 40 wt.% FA1 and 60 wt.% FA1, respectively. As shown in Figure 4, the 28-day strength of H1-1 and H1-2 samples reached 21.2 and 12.5 MPa, respectively. Nevertheless, the strengths of OF1 and OF2 samples were just 9.3 and 6.1 MPa, respectively, at the same FA1 contents. The results indicated that the strength of binder-FA1 blocks had an increase of 104.92-127.96% by using MSCM to replace OPC as the binder. It also suggested that the MSCM, prepared from industrial wastes, achieved higher cementitious reactivity in the solidification/stabilization of MSWI fly ash than OPC.
As given in Table 5, the leaching concentrations of Zn, Cr, Pb and Hg were just in range of 1.17-25.64 μg/L for all MSCM-fly ash blocks, much lower than the limited va of the Chinese landfill standard (GB 16889-2008), as listed in Table 3. Taking the FA an example, the leaching concentrations of Pb and Zn reached 46,400 and 5080 μg/L original FA1, respectively. By solidifying FA1 with the addition of 40 wt.% MSCM (H sample), the Pb and Zn concentrations decreased significantly to only 25.64 and 3.31 μ respectively. For all MSWI fly ashes, the immobilization rates of Zn, Cr, and Pb excee 99.90% and that of Hg reached above 98.70% at 60 wt.% fly ash. Based on the above res it is suggested that the solidification/stabilization of MSWI fly ashes from different c by using novel MSCM as a low-carbon binder could achieve high strength of fly ash bl and low leachability of heavy metals.

Comparison of MSWI Fly Ash Solidification by MSCM and OPC
In this case, the solidification/stabilization treatment of FA1 by MSCM and OPC compared. Due to high-leaching concentrations of Zn, Pb, and Hg, as seen in Table 3 FA1 was selected as the typical MSWI fly ash for the comparison. For the solidification bilization treatment by OPC, the OF1 and OF2 samples represented OPC-fly ash bl with 40 wt.% FA1 and 60 wt.% FA1, respectively. As shown in Figure 4, the 28 strength of H1-1 and H1-2 samples reached 21.2 and 12.5 MPa, respectively. Neverthe the strengths of OF1 and OF2 samples were just 9.3 and 6.1 MPa, respectively, at the s FA1 contents. The results indicated that the strength of binder-FA1 blocks had an incr of 104.92-127.96% by using MSCM to replace OPC as the binder. It also suggested tha MSCM, prepared from industrial wastes, achieved higher cementitious reactivity in solidification/stabilization of MSWI fly ash than OPC.    Figure 5 showed the leaching concentrations of heavy metals in FA1 blocks solidified by MSCM and OPC, respectively. Except for the Hg element, the leaching concentrations of Zn, Cr, and Pb decreased at longer curing times while either MSCM or OPC was used as the binder. For all heavy metals, the MSCM-FA1 blocks achieved lower leaching concentrations than OPC-FA1 blocks. Taking Zn and Pb elements as examples, the leaching concentrations decreased from 55.91 to 3.31 µg/L and from 39.14 to 25.64 µg/L, respectively, by using MSCM to replace OPC to solidify FA1 at 60 wt.% content. Accordingly, it is well suggested that the MSCM could achieve higher mechanic strength and lower leaching concentrations of heavy metals than widely used OPC in the solidification/stabilization of MSWI fly ash.
centrations than OPC-FA1 blocks. Taking Zn and Pb elements as examples, the leaching concentrations decreased from 55.91 to 3.31 μg/L and from 39.14 to 25.64 μg/L, respectively, by using MSCM to replace OPC to solidify FA1 at 60 wt.% content. Accordingly, it is well suggested that the MSCM could achieve higher mechanic strength and lower leaching concentrations of heavy metals than widely used OPC in the solidification/stabilization of MSWI fly ash.

Formation of Hydration Products
Generally, the immobilization of heavy metals in MSWI fly ash was highly related to hydration products formed through numerous reactions of components in binder-fly ash pastes. In this study, pure MSCM paste (100 wt.% MSCM + 0 wt.% FA2, D0 sample) and MSCM-fly ash paste (60 wt.% MSCM + 40 wt.% FA2, D4 sample) were prepared to investigate the formation of hydrates. As shown in Figure 6a, the hydrates, including portlandite, calcium silicate hydrate (C-S-H), and ettringite (AFt), appeared in the hardened MSCM paste. After 60 wt.% MSCM was mixed with 40 wt.% FA2, the stratlingite (C-A-S-H) and Friedel's salt were formed as new hydrates, as shown in Figure 6b, resulting in a denser microstructure in MSCM-fly ash blocks. However, no typical diffraction peaks of

Formation of Hydration Products
Generally, the immobilization of heavy metals in MSWI fly ash was highly related to hydration products formed through numerous reactions of components in binder-fly ash pastes. In this study, pure MSCM paste (100 wt.% MSCM + 0 wt.% FA2, D0 sample) and MSCM-fly ash paste (60 wt.% MSCM + 40 wt.% FA2, D4 sample) were prepared to investigate the formation of hydrates. As shown in Figure 6a, the hydrates, including portlandite, calcium silicate hydrate (C-S-H), and ettringite (AFt), appeared in the hardened MSCM paste. After 60 wt.% MSCM was mixed with 40 wt.% FA2, the stratlingite (C-A-S-H) and Friedel's salt were formed as new hydrates, as shown in Figure 6b, resulting in a denser microstructure in MSCM-fly ash blocks. However, no typical diffraction peaks of portlandite and AFt were observed in D4 samples, which indicated the occurrence of further hydration reactions of these hydrates with the components in FA2. Since the AFt can significantly promote developing the strength of harden paste, the disappearance of AFt in the D4 sample could well explain the decreased strength of MSCM-fly ash blocks at higher FA2 contents, as shown in Figure 2. As shown in Figure 6b, the diffraction peak intensities of KCl and NaCl became lower at longer curing times. It seemed that soluble chloride salts were partially consumed to form Friedel's salt, as confirmed by XRD [28].
portlandite and AFt were observed in D4 samples, which indicated the occurrence of further hydration reactions of these hydrates with the components in FA2. Since the AFt can significantly promote developing the strength of harden paste, the disappearance of AFt in the D4 sample could well explain the decreased strength of MSCM-fly ash blocks at higher FA2 contents, as shown in Figure 2. As shown in Figure 6b, the diffraction peak intensities of KCl and NaCl became lower at longer curing times. It seemed that soluble chloride salts were partially consumed to form Friedel's salt, as confirmed by XRD [28]. The microstructures of D4 samples after three days, seven days, and twenty-eight days of hydration are shown in Figure 7. After curing for three days, colloidal C-S-H gels were generated in the MSCM-FA2 block. In addition, the ettringite (AFt) with the typical structures of cloudy filaments or needle rods also appeared [26,27]. By extending curing time to seven days, the amounts of C-S-H gels seemed to increase, and the C-A-S-H appeared. However, the filament-or rod-like AFt phase disappeared, which was consistent with minerals phases determined by XRD. At the curing time of 28 days, more C-S-H and C-A-S-H were coated on the particle surface, promoting the strength development of the FA2 block. The microstructures of D4 samples after three days, seven days, and twenty-eight days of hydration are shown in Figure 7. After curing for three days, colloidal C-S-H gels were generated in the MSCM-FA2 block. In addition, the ettringite (AFt) with the typical structures of cloudy filaments or needle rods also appeared [26,27]. By extending curing time to seven days, the amounts of C-S-H gels seemed to increase, and the C-A-S-H appeared. However, the filament-or rod-like AFt phase disappeared, which was consistent with minerals phases determined by XRD. At the curing time of 28 days, more C-S-H and C-A-S-H were coated on the particle surface, promoting the strength development of the FA2 block.  Figure 8 showed the DTG curves of D4 samples after curing for three, seven, and twenty-eight days. The endothermic peaks at 118 °C (3 days), 93 °C (7 days), and 100 °C (28 days) could be assigned to dehydration of free water in hydrates, such as C-S-H gels  Figure 8 showed the DTG curves of D4 samples after curing for three, seven, and twenty-eight days. The endothermic peaks at 118 • C (3 days), 93 • C (7 days), and 100 • C (28 days) could be assigned to dehydration of free water in hydrates, such as C-S-H gels and AFt [29]. The endothermic peaks between 250 and 350 • C were related to the decomposition of C-S-H gels or C-A-S-H to release crystal water [30]. The change of endothermic peaks located at 250~350 • C might be attributed to the crystalline structure changes due to the incorporation of heavy metal ions in C-S-H or C-A-S-H hydrates [31,32]. The calcite was detected at endothermic peaks of 853 and 867 • C after curing for three days. The peaks at approximately 650 • C could be attributed to the crystal transformation of calcium silicates (e.g., C 3 S and C 2 S) [33]. . Figure 8. DTG curves of D4 samples after curing for 3, 7, and 28 days.

Immobilization Mechanisms of Heavy Metals
The immobilization mechanisms of heavy metals in MSWI fly ash were quite complex for cement-based solidification/stabilization treatment, including adsorption, isomorphous replacement, chemical precipitation, surface complexation, and physical encapsulation [34,35]. In this case, the hydration of pure MSCM pastes resulted in the formation of C-S-H gel, Aft, and Ca(OH)2, which could immobilize heavy metals via adsorption, cation exchange, and physical encapsulation [35][36][37][38]. In MSCM-fly ash blocks, new phases, such as C-A-S-H and Friedel's salt, appeared due to the interference of fly ash. The C-A-S-H was the zeolite-like mineral composed of oxygen-silicon tetrahedron, achieving strong capacity of adsorption and ion exchange due to the ultra-large specific surface area [35]. Cation metal ions, such as Pb 2+ and Cr 3+ , could be effectively adsorbed by the C-A-S-H. Additionally, generated Friedel's salt could participate into the immobilization of heavy metals in MSCM-fly ash blocks [39]. In this study, the precipitation of insoluble metallic phosphates (e.g., Pb3(PO4)2, Pb10(PO4)6(OH)2) might also contribute to the immobilization of cation heavy metal ions due to the high content of P2O5 (21.76 wt.%) in phosphoric acid sludge [40,41]. Therefore, heavy metals in MSCM-fly ash blocks could be effectively immobilized via multi-pathways in the hydration process.

Conclusions
In this work, four industrial wastes, i.e., blast furnace slag, steel slag, desulfurization ash, and phosphoric acid sludge, were used to prepare a low-carbon binder, metallurgical

Immobilization Mechanisms of Heavy Metals
The immobilization mechanisms of heavy metals in MSWI fly ash were quite complex for cement-based solidification/stabilization treatment, including adsorption, isomorphous replacement, chemical precipitation, surface complexation, and physical encapsulation [34,35]. In this case, the hydration of pure MSCM pastes resulted in the formation of C-S-H gel, Aft, and Ca(OH) 2 , which could immobilize heavy metals via adsorption, cation exchange, and physical encapsulation [35][36][37][38]. In MSCM-fly ash blocks, new phases, such as C-A-S-H and Friedel's salt, appeared due to the interference of fly ash. The C-A-S-H was the zeolite-like mineral composed of oxygen-silicon tetrahedron, achieving strong capacity of adsorption and ion exchange due to the ultra-large specific surface area [35]. Cation metal ions, such as Pb 2+ and Cr 3+ , could be effectively adsorbed by the C-A-S-H. Additionally, generated Friedel's salt could participate into the immobilization of heavy metals in MSCM-fly ash blocks [39]. In this study, the precipitation of insoluble metallic phosphates (e.g., Pb 3 (PO 4 ) 2 , Pb 10 (PO 4 ) 6 (OH) 2 ) might also contribute to the immobilization of cation heavy metal ions due to the high content of P 2 O 5 (21.76 wt.%) in phosphoric acid sludge [40,41]. Therefore, heavy metals in MSCM-fly ash blocks could be effectively immobilized via multi-pathways in the hydration process.

Conclusions
In this work, four industrial wastes, i.e., blast furnace slag, steel slag, desulfurization ash, and phosphoric acid sludge, were used to prepare a low-carbon binder, metallurgical slag-based cementing material (MSCM). Then, the solidification/stabilization of MSWI fly ashes were evaluated by using MSCM as the binder.
(1) The MSCM exhibited high-hydration reactivity, achieving 3-day and 28-day strengths of 26.9 and 35.2 MPa for pure MSCM pastes, respectively. While the FA2 content was as high as 80 wt.%, the 28-day strength of MSCM-FA2 blocks reached 2.2 MPa, and the leaching concentrations of Zn, Cr, Hg, and Pb were far below the limit values of the Chinese landfill standard (GB 16889-2008). The immobilization rates of Zn, Cr, and Pb were above 99.90%, and that of Hg was above 98.70% for tour kinds of MSWI fly ashes. Heavy metals in MSWI fly ash could be effectively immobilized via adsorption, cation exchange, precipitation, and physical encapsulation.
Supplementary Materials: The following supporting information can be downloaded at: https: //www.mdpi.com/article/10.3390/min12050599/s1, Figure S1: XRD patterns of blast furnace slag (a), steel slag (b), desulfurization ash (c), and phosphoric acid sludge (d); Table S1: The comprehensive strength of pure MSCM pastes with different proportions of raw materials; Table S2: Main chemical compositions of four kinds of MSWI fly ashes.

Data Availability Statement:
The data presented in this study are available on request from the corresponding author.

Conflicts of Interest:
The authors declare no conflict of interest.