A Porous Geopolymer Containing Ti-Bearing Blast Furnace Slag: Synthesis, Characterization, and Adsorption-Photodegradation Studies towards Methylene Blue Removal under Visible Light Condition

Abstract

A porous geopolymer with adsorption and photocatalytic degradation functions was successfully developed by utilizing Ti-bearing blast furnace slag (TBBFS) as the raw material. The prepared porous geopolymers were characterized by X-ray diffraction, scanning electron microscope, energy dispersive spectrometer, and Fourier transform infrared spectrum. Selective crystallization, water quenching, and natural cooling methods were employed to investigate the influences of these modifications on the applicability of TBBFS as a precursor for geopolymer synthesis. Water-quenched slag with amorphous content was prone to alkali dissolution, and the resulting geopolymer exhibited the highest adsorption capacity (97.18 mg/g) for methylene blue (MB) removal. Selective crystallization at 1400 °C generated a hybrid microstructure consisting of a non-cementitious CaTiO₃ crystallization phase and a cementitious amorphous fraction. The retention of CaTiO₃ in the final geopolymer enables a bifunctionality in adsorption–photodegradation. Particularly, the adsorption and photodegradation processes under various conditions were investigated. The superior removal efficiency for MB could be attributed to the synergistic effects between the geopolymer matrix and CaTiO₃, leading to an enhancement in the formation of hydroxyl radicals. The conversion of TBBFS into porous geopolymer offers an efficient and straightforward solution for slag utilization and dye removal.

1. Introduction

China holds more than half of the world’s total titanium reserves, with approximately 90% located in the Panxi region in the form of vanadium–titanium magnetite [1]. Over 3-million tons of Ti-bearing blast furnace slag (TBBFS) are generated annually when vanadium–titanium magnetite is melted for iron production [2,3]. The inappropriate disposal of TBBFS cannot only be hazardous to the environment but also lead to a potential waste of titanium resources [4]. Recently, the conversion of TBBFS into photocatalytic materials (TiO₂, CaTiO₃) has garnered significant attention and can be achieved through alkali fusion and acid leaching [5,6]. Lü et al. [7] converted TBBFS to a visible-light-responsive photocatalyst CaTiO₃ by thermal treatment with NaNO₃, followed by HCl leaching. Similarly, Li et al. [8] fabricated nanostructured TiO₂ photocatalysts with diverse crystal morphologies by subjecting TBBFS to molten NaOH treatment, water leaching, and hydrolysis procedures. Despite numerous successful attempts, the preparation of the photocatalyst mentioned above requires the extraction of Ti from TBBFS via intricate processing stages, which inherently possess drawbacks of high operational and handling costs. Simultaneously, other components inevitably result in highly hazardous sludge and are not fully utilized. Furthermore, due to environmental concerns, the processing sludge presents additional treatment and disposal challenges. Hence, it is crucial to improve the conversion process by developing an eco-friendly and effective methodology for the value-added utilization of TBBFS.

Geopolymers are inorganic polymeric materials synthesized by aluminosilicate sources such as granulated blast furnace slag (GBFS), metakaolin (MK), and fly ash (FA) [9]. In recent years, geopolymers have attracted considerable attention as a new type of sustainable material due to their potential applications in cement, concrete, and environmental remediation [10,11,12]. Porous geopolymers have been proven to be capable of adsorbing toxic and harmful organic substances [9,13]. Furthermore, the introduction of a photocatalyst into geopolymer imparts photocatalytic activity that enables the pollutants to be photodegraded. Maiti et al. [14] successfully prepared a photocatalytic geopolymer by mixing TiO₂ nanoparticles with fly ash, alkali activator, and normal sands. In addition, to improve the mechanical properties of modified geopolymer, the incorporation of nano TiO₂ exhibited a considerable removal efficiency of methylene blue (MB) dye (96.4% degradation in 90 min). Li et al. [15] prepared geopolymer spheres by suspension solidification and facilitated the growth of CdS on the surface of geopolymer spheres by van der Waals forces and ion–exchange interactions. The degradation efficiency for methyl orange of the material reaches approximately 92.57%. Falah et al. [16] prepared novel photoactive composites for the destruction of organic pollutants by blending the uncured geopolymer mixture with Cu₂O/TiO₂ nanospheres. After 12 h of adsorption in dark and 4 h of photodegradation under UV irradiation, the removal efficiency of MB reached 99%. These studies demonstrated that geopolymers could be employed not only as adsorbents but also combined with semiconductor materials to create a new composite material that can exhibit both adsorption and photocatalytic degradation functions.

TBBFS typically comprises oxides of CaO, SiO₂, MgO, etc., while the content of TiO₂ is 12–28 wt.%. TBBFS has the advantage of high Ti content and utilizes Ti components. Previous studies have proven that implementing slag modification combined with selective crystallization allows for the enrichment of Ti in the form of a perovskite phase, while the remaining components exist in an amorphous state [4,17]. Based on this, we proposed a facile and straightforward methodology for manufacturing photocatalytic porous geopolymers from TBBFS. By applying selective crystallization to TBBFS at a high temperature (1400 °C), the solely precipitated CaTiO₃ can be acted as a promising photocatalytic material [18], while the amorphous glassy components can be employed as a precursor for geopolymer formation. During geopolymerzation, CaTiO₃ will remain intact due to its high chemical stability against alkali dissolution, thereby providing photocatalytic activity in the resulting geopolymer. Currently, geopolymers are often utilized in organic wastewater treatment in the form of monoliths, spheres, and powders [15,19,20]. However, geopolymer powders exhibit characteristics such as small particles, uniform distribution in wastewater, and rapid action time. Compared to conventional methods, the proposed approach has the advantages of (i) Reduced environmental risk, as no Ti extraction methods are employed; (ii) Full utilization of all components in TBBFS; and (iii) More effective adhesion between CaTiO₃ and geopolymer matrix compared to simply mixing.

The properties of geopolymer can vary significantly depending on the synthesis parameters, raw materials, and mixed proportions. In the context of slag reactivity, it is reasonable to expect the differences as the aluminosilicate species participate in either glassy or crystalline structure. Hence, in addition to selective crystallization, water quenching and natural cooling were also employed to investigate the influences of these cooling paths on the applicability of TBBFS as a precursor for geopolymer synthesis. Most importantly, these thermal treatments for TBBFS modification are easily scalable to implement at an industrial scale, which is crucial for the practical realization of this promising process. In this study, the effects of processing parameters on the phase transformations, microstructure, and textural properties of the geopolymer were systematically studied. The obtained geopolymer exhibited a high specific surface area, abundant porous structure, and high photocatalytic activity, which were applied for the removal of MB, providing further environmental benefits.

2. Results and Discussion

2.1. Mineralogy and Reactivity of Modified TBBFS

Figure 1A illustrates the simulated equilibrium solidification of TBBFS with temperature using Fact–Sage software. The perovskite phase began to precipitate solely at 1410 °C, and its content gradually increased as the temperature decreased. This indicates that the selective crystallization of perovskite can be achieved using the as-received TBBFS without further compositional adjustments. According to the thermodynamic prediction, the optimal temperature for selective crystallization would be close to 1410 °C. The XRD analysis in Figure 1B confirmed that the thermal modification at 1400 °C for 1 h resulted in the precipitation of perovskite from vitreous slag. However, the minor phase crystalline peaks assigned to aluminum spinel MgAl₂O₄ (JCPDS 82-2424) also appeared, probably due to its high melting point. In the natural-cooled slag, minerals of perovskite, augite (Ca(Mg,Fe,Al,Ti)(Si,Al)₂O₆), and spinel were precipitated. The deviation from predicted mineralogy based on thermodynamic calculations is due to limited mass transfer during the actual cooling process. Conversely, the water-quenched slag underwent a rapid cooling rate, and its mineralogy was predominantly glassy, as no diffraction peaks were observed. By analyzing the microstructure and corresponding EDS results (Figure S1, Table S1), the enrichment of Ti in perovskite would result in a relatively lower Ca and Ti and higher Si and Al content in the glassy matrix, which was inferred to possess a higher reactivity in geopolymerization.

The modified slags were used as precursors for geopolymerization and subjected to alkali activation. The leaching concentration of metal ions in alkaline solution can be employed as an indicator for evaluating the reactivity of the modified slags [19,20]. Figure 2 demonstrated the leaching result of different modified slags in alkaline solution; the leaching concentration of Al and Si were the highest in S–W and the lowest in S–N. Compared with crystalline phases, the three-dimensional networks of amorphous phase possess lower binding energy for Al–O and Si–O bonds [21], rendering them more susceptible to dissolution under alkaline attack. This suggests that the reactivity of slag in geopolymerization is positively correlated with the amorphous fraction possessing cementitious properties. Considering the XRD analysis and dissolution results, the reactivity of modified slags follows the order of S–W > S–1400 °C–1.0 h > S–N.

Additionally, it was observed that the alkali activation resulted in the dissolution of Ca, which is an inherent element presented in TBBFS. The prolongation of alkali activation did not benefit Ca dissolution; on the contrary, Ca concentration decreased. Ca was either precipitated as Ca(OH)₂ or converted into C–A–S–H/C–S–H gel by reacting with the dissolved silicate and aluminate species [21]. Under a high concentration of alkali activator, it is plausible that leached Ca²⁺ reacts with OH^- to form Ca(OH)₂ precipitation.

2.2. The Structural Properties and Morphology of Porous Geopolymer

As verified in Figure S1, the modified slag of S–1400 °C–1.0 h is consisted of crystallized CaTiO₃ and a glassy matrix. The structure of geopolymer M-20H/N-0.50P-3%H₂O₂ was corroborated through powder XRD analysis. As shown in Figure 3A, typical peaks of crystalline phases CaTiO₃, MgAl₂O₄, and mullite were detected, and the latter originated from thermally activated kaolin (Figure S2). The retention of CaTiO₃ confirmed its non-cementitious nature during geopolymerization. A broad diffraction hump near 30°, which is a characteristic feature of the amorphous phase, indicated structural changes that occurred when the raw materials reacted to form geopolymeric gel with the incorporation of the alkali solution [22,23].

FTIR spectra of the geopolymer M-20H/N-0.50P-3%H₂O₂ was displayed in Figure 3B. The signal at 460 cm⁻¹ and 500 cm⁻¹ can be related to Al–O/Si–O. A clear stretching and bending vibration of Ca–O–Ti at 580 cm⁻¹ indicates the presence of CaTiO₃. A band located at 981 cm⁻¹ was attributed to the bending vibration of Si–O–Al or the stretching vibration of Ti–O–Si. Meanwhile, the elongation of O–H bonds can be associated with the signals at 3450 and 1630 cm⁻¹, which can be attributed to the presence of water molecules in the material [24]. The signal at 1462 cm⁻¹ is the tensile vibration of O–C–O [25], mainly due to the interaction between the particle surface and atmospheric CO₂.

The particle morphology of geopolymer M-20H/N-0.50P-3%H₂O₂ was investigated by SEM. In Figure 4A, the 70 μm-sized particles were undissolved and likely originated from TBBFS. The elemental mapping results suggested the rhomboid grains embedded in the undissolved residual particle were rich in Ca and Ti elements, which can be assigned to CaTiO₃ crystals. The irregular particles in Figure 4B exhibit amorphous assembly, where nano-scale particles are observed at the surface. These formed gels, or nano-crystals, could act as binder phases and bond with undissolved particles [26].

UV–Vis–DRS was measured to describe the photo-adsorption behavior (Figure S3A). Synthetic CaTiO₃ exhibited strong ultraviolet light absorption with a wide bandgap energy of 3.28 eV (Figure S3B). Slag S–1400 °C–1.0 h and geopolymer M-20H/N-0.5P-3%H₂O₂ exhibited a slight increase in the visible light absorption, as indicated by narrower bandgap energies [27]. These results may be due to the red shift resulting from the effect of transition metal ions and nonmetal elements in the samples [7]. Additionally, in the subsequent photocatalytic degradation of MB, due to the synergistic effect of CaTiO₃ and OH⁻, the actual photocatalytic degradation performance was significantly better than CaTiO₃ and modified slag. The details are discussed later in Section 2.4.

The N₂ adsorption–desorption curves were adopted to determine the textural properties. As shown in Figure S4, the prepared samples presented a Type IV isotherm with a Type H3 hysteresis loop, which indicates a slit-shaped mesoporous structure.

Table 1. Textural properties of porous geopolymers.

Material	SBET (m2/g)	Pore Volume (cm3/g)	Average Pore Size (nm)
M-12H/N-0.50P-3%H2O2	52.24	0.143	9.75
M-16H/N-0.50P-1%H2O2	56.12	0.208	11.32
M-16H/N-0.50P-3%H2O2	60.74	0.202	11.79
M-16H/N-0.50P-5%H2O2	72.33	0.191	10.16
M-20H/N-0.50P-3%H2O2	80.32	0.227	10.93
M-20H/N-0.25P-3%H2O2	87.58	0.253	11.31
M-20H/N-0.75P-3%H2O2	62.44	0.184	9.97
W-20H/N-0.50P-3%H2O2	91.52	0.219	9.22
N-20H/N-0.50P-3%H2O2	66.27	0.217	12.06

shows that the specific surface area (S_BET), average pore size, and pore volume are in the range of 52.24~91.52 m²/g, 9.22~12.06 nm, and 0.143~0.253 cm³/g, respectively. The addition of H₂O₂ can increase the specific surface area of geopolymers. The specific surface areas of the geopolymers prepared under 1 wt.%, 3 wt.%, and 5 wt.% H₂O₂ were 56.12 m²/g, 60.74 m²/g, and 72.33 m²/g, respectively. Meanwhile, the n(H₂O)/n(Na) had little effect on the specific surface area. When increasing from 12 to 20, the specific surface area of the geopolymer only increased from 52.24 m²/g to 80.32 m²/g. Due to the lower activity of modified slag compared to metakaolin and fumed silica, when a high volume of TBBFS was introduced as a precursor in alkaline activation, the specific surface area of the resulting geopolymer decreased. According to the previous analysis of the reactivity of different slag precursors, the prepared geopolymer-specific surface area obtained consistent results. Still, geopolymer M-20H/N-0.50P-3%H₂O₂ exhibited a high BET surface area of 80.32 m²/g.

2.3. The Effect of Processing Parameters on the Adsorption-Photocatalytic Degradation Behavior

The MB removal tests were performed independently in the dark and under a visible light source. The difference in the MB removal efficiency between different geopolymers was shown in Figure 5. The adsorption–desorption equilibrium can be well-established in 120 min, independent of various conditions. The adsorption towards MB removal benefited from higher n(H₂O)/n(Na), the addition of H₂O₂, and the low proportional use of modified slag. The order of adsorption capacity of geopolymer is successively W-20H/N-0.50P-3%H₂O₂ > M-20H/N-0.50P-3%H₂O₂ > N-20H/N-0.50P-3%H₂O₂. It implies that higher S_BET with more available sites favors MB adsorption. As for the photocatalytic activity, it will be discussed later in Section 2.3.4.

2.3.1. Adsorption Kinetic Characteristics

The geopolymers derived from modified slags, i.e., S–1400 °C–1.0 h, S–W were selected to study their adsorption kinetics, which helps us to comprehend the underlying interactions between adsorbents and adsorbates. Figure 6 displays the kinetic curves of geopolymer M-20H/N-0.50P-3%H₂O₂ and W-20H/N-0.50P-3%H₂O₂ at different temperatures. It was found that temperature increments did not enhance adsorption capacity but shortened the time to attain equilibrium, suggesting the adsorption is exothermic [28]. The equations of the models were presented in the Supplemental Materials. The fitting results in Figure 7 show that the pseudo-second-order model presents the highest correlation coefficient, which signifies that the chemical interactions between MB molecules and the geopolymer surface are the rate-limiting step [29].

2.3.2. Adsorption Thermodynamics

Adsorption thermodynamic parameters, i.e., equilibrium constant (K_C, L/mg), Gibb’s free energy change (ΔG, KJ/mol), and enthalpy change (ΔH, KJ/mol), as well as entropy change (ΔS, KJ/(K·mol)), were assessed to evaluate the feasibility, nature, and favorability of adsorption.

$$K_C=\frac{Q_e}{C_e}$$

(1)

$$\Delta G=-RT\ln K_C$$

(2)

$$\ln K_c=-\frac{\Delta H}{RT}+\frac{\Delta S}{R}$$

(3)

In Equations (1)–(3) [30]: Q_e: the amount of MB dye per unit mass of absorbent at equilibrium, mg/g; C_e: equilibrium concentration of MB in solution, mg/L; R: ideal gas constant, 8.314 J/(mol·K); T: thermodynamic temperature, K.

The results for adsorption thermodynamics are presented in

Table 2. Adsorption thermodynamic parameters of geopolymers.

Material	T (K)	KC	ΔG (kJ/mol)	ΔH (kJ/mol)	ΔS (kJ/K·mol)
M-20H/N-0.50P-3%H2O2	293	21.000	−7.416	−56.37328	−0.16678
	303	10.316	−5.879
	313	5.412	−4.394
	323	2.381	−2.330
W-20H/N-0.50P-3%H2O2	293	19.647	−7.254	−7.94761	−0.00234
	303	17.730	−7.243
	313	16.100	−7.231
	323	14.483	−7.178

and Figure S5. The adsorption process of geopolymers onto MB is exothermic, as indicated by a negative value of enthalpy change ΔH. The negative ΔG value indicates that the adsorption is a thermodynamic spontaneous process. As the temperature increases, its value rises, while the corresponding equilibrium constant decreases, signifying that higher temperature is unfavorable for adsorption.

2.3.3. Adsorption Isotherms

The adsorption isotherms were conducted under the conditions of 20 °C, 120 min, and 20 mg of adsorbent to investigate homogeneous or heterogeneous adsorption behavior. As seen in Figure 8, the Q_e values for geopolymer M-20H/N-0.50P-3%H₂O₂ and W-20H/N-0.50P-3%H₂O₂ increase with rising initial concentration, while the removal rate of MB decreases. The Langmuir model [31], Freundlich model [32], and Temkin model [33] (represented by the L model, F model, and T model) were adopted to fit the adsorption isotherms, with equations detailed in the Supplement Materials.

As illustrated in Figure S6 and

Table 3. Isotherms parameters for MB adsorption on geopolymers.

Isotherm	Parameters	M-20H/N-0.50P-3%H2O2	W-20H/N-0.50P-3%H2O2
L model	Q0 (mg/g)	59.31	97.18
	KL (L/mg)	2.01	1.22
	R2	0.99956	0.99114
F model	n	3.87	6.45
	KF (L/g)	52.59	39.74
	R2	0.50760	0.86593
T model	B (J/mole)	7.35	16.66
	A (L/g)	224.18	26.77
	R2	0.88322	0.57132

, the fitting results indicate that the adsorption isotherms are well-described by the Langmuir model, suggesting that the adsorption is monolayer adsorption. The maximum adsorption capacity (Q₀, mg/L) calculated using the L model is 59.31 mg/g at 20 °C for geopolymer M-20H/N-0.50P-3%H₂O₂, and 97.18 mg/g for geopolymer W-20H/N-0.50P-3%H₂O₂.

Furthermore, a direct comparison of MB adsorption capacities with S_BET among different materials is conducted. The results in

Table 4. Comparison of adsorption capacity of various absorbents for MB removal.

Adsorbents	Temperature (°C)	BET Surface Area (m2/g)	Adsorption Capacity (mg/g)	Ref.
Phosphoric acid-based geopolymer	28	2.28	3.01	[33]
Moroccan clay-based geopolymer	-	128	183	[34]
Biomass fly ash-geopolymer monoliths	-	-	15.4 (1st), 20.5 (2nd), 20.4 (3rd)	[35]
Fly ash geopolymer balls	Ambient temperature	-	30.1 (1st), 79.7 (9th)	[36]
M-20H/N-0.50P-3%H2O2	20	72.33	59.31	This work
W-20H/N-0.50P-3%H2O2	20	91.52	97.18	This work

indicate that the MB adsorption capacity is strongly correlated with the specific surface area of the materials. Moroccan clay-based geopolymer with a high S_BET of 128 m²/g exhibited an adsorption capacity of 183 mg/g [34]. Studies by Novais et al. [35] verified that the adsorption capacity of geopolymer can be enhanced through a thermal regeneration process. The adsorption capacity of fly ash geopolymer spheres increased from 30.1 mg/g (1st) to 79.9 mg/g (9th) [36]. Compared to other reported materials, the as-prepared geopolymers from TBBFS possess high S_BET and excellent adsorption performance for MB removal.

2.3.4. Photodegradation Kinetics

To assess the photocatalytic activities of the prepared geopolymers, synthesized CaTiO₃ was selected for comparison. As shown in Figure 9A–D, the ln(C/C_e) plotted against light irradiation time exhibits a linear relationship, revealing that degradation curves of MB follow pseudo-first-order kinetics, which align with the Langmuir–Hinshelwood (L–H) model when the solution is diluted (<1 × 10⁻³) [37,38,39].

$$-\ln \left(\frac{C}{C_e}\right)=k_{ap}t$$

(4)

where C is the concentration of MB at time interval t under visible light illumination (mg/L), k_ap is the apparent rate constant of a pseudo-first-order reaction (min⁻¹).

The self-decomposition of MB under visible light irradiation (blank: without catalyst) is negligible. Compared to that of pure CaTiO₃, the degradation efficiencies for MB substantially improve when geopolymer material is added to MB solution, except for material W-16H/N-0.50P-3%H₂O₂. Figure 9A–C reveal that processing parameters, i.e., n(H₂O)/n(Na), the addition of H₂O₂, and the use of modified slag, positively affect the enhancement of photocatalytic activity.

As seen in

Table 5. Comparison of photocatalytic performance of various materials for MB removal.

Photocatalyst	Catalyst Dose (mg) vs. vol (mL) and MB Conc (mg/L)	Performance	kap (min−1)	Ref.
CaTiO3/Ca(OH)2	100 vs. 100 of 10−5 mol/L	82.3% degradation in 8 min	0.2168	[40]
CaTiO3	100 vs. 200 of 10	44.29% degradation in 325 min	0.0018	[41]
HNO3 acidified CaTiO3 (pH = 2)	100 vs. 200 of 10	66.86% degradation in 325 min	0.00359	[41]
Graphite oxide grafted titanate nanotubes	20 vs. 100 of 20	97.5% degradation in 120 min (30 min adsorption and 90 min UV irradiation)	0.02845	[42]
CuO@calcium silicate hydrate	20 vs. 50 of 20	90% degradation in 150 mi	0.0119	[43]
CaTiO3	50 vs. 200 of 20	52.24% degradation in 180 min	0.00379	This work
S-N	50 vs. 200 of 20	57.63% degradation in 180 min	0.00437	This work
S-1400 °C–1.0 h	50 vs. 200 of 20	54.41% degradation in 180 min	0.00390	This work
N-20H/N-0.50P-3%H2O2	50 vs. 200 of 20	87.56% degradation in 180 min	0.0084	This work
M-20H/N-0.50P-3%H2O2	50 vs. 200 of 20	93.5% degradation in 180 min	0.01115	This work

, a comparison of MB removal performance and apparent rate constant k_ap, among various materials, was made. CaTiO₃ typically possesses a large bandgap energy and exhibits photocatalytic activity under ultraviolet light irradiation. By combining Ca(OH)₂, the CaTiO₃/Ca(OH)₂ composite exhibits a superior photocatalytic activity with a k_ap value of 0.2168 min⁻¹ under ultraviolet light irradiation [40]. However, under visible light irradiation, even after HNO₃ acidification, modified CaTiO₃ exihibits a slightly higher k_ap value of 0.00359 min⁻¹ compared to unmodified CaTiO₃ [41]. Considering the adsorption–photocatalytic degradation performance in Figure S7 and Table 5, the obtained geopolymers were demonstrated to be promising candidates for dye removal. The k_ap values of modified slag of S–1400 °C–1.0 h and S–N are comparable to that of pure CaTiO₃. Geopolymer M-20H/N-0.5P-3%H₂O₂ exhibits enhanced photocatalytic activity with a considerably higher k_ap value of 0.01115 min⁻¹, implying that the visible light photocatalytic efficiency for MB reaches 93.5% in 180 min with a geopolymer dosage of 50 mg.

2.4. Possible Interaction Mechanism

The possible interaction between porous geopolymer and MB is illustrated in Figure 10. The adsorptive–photocatalytic process of MB removal comprises successive steps: (i) The mass transfer of MB molecules from the liquid phase to the geopolymer surface via external and intraparticle diffusion; (ii) The chemisorption of MB on the surface via surface interactions; and (iii) The photodegradation of MB by CaTiO₃. As a cationic dye, the adsorption of MB molecules is facilitated by the negatively charged surface of adsorbents [44,45].

Table 6. The pH changes during the removal process of MB by geopolymers.

	pH Initial	pH Adsorption Equilibrium	Photodegradation Time (min)
			20	40	60	80	100	140	180
M-12H/N-0.50P-3%H2O2	10.02	10.02	9.84	9.61	9.47	9.29	9.11	8.71	8.28
M-16H/N-0.50P-3%H2O2	9.97	9.97	9.78	9.60	9.46	9.26	9.09	8.67	8.25
M-20H/N-0.50P-3%H2O2	9.93	9.93	9.75	9.59	9.45	9.24	9.05	8.63	8.21

illustrates the pH changes of the MB solution during the adsorption–photodegradation process. After the addition of geopolymer powders to the MB solution, the pH value of the slurry increased to approximately 10 due to the leaching of OH⁻. The geopolymer can act as a pH buffer by releasing hydroxyl ions in the waste treatment system [46]. This suggested that the cationic MB⁺ can absorb easily onto the geopolymer because of electrostatic attraction, forming hydrogen bonds between a hydroxyl group (-OH) and a nitrogen atom in the MB molecule [44].

When the illuminated light energy is larger than the bandgap of CaTiO₃, CaTiO₃ absorbs the light energy to form photogenerated electron-hole pairs (Equation (5)) at the surface of particles. To prevent the recombination of electron-hole pairs, they have to participate in the redox reactions by combining with the oxidant (Equations (6) and (7)) and reductant (Equation (8)), respectively. According to the pH variation in Table 6, its value gradually decreased, along with the photodegradation process. This indicated that the OH^- released by geopolymer was consumed by photogenerated holes to generate strong oxidative ·OH radicals.

$${\mathrm{CaTiO}}_3+\mathrm{hv}\to {\mathrm{e}}^{-}+{\mathrm{h}}^{+}$$

(5)

$${\mathrm{e}}^{-}+{\mathrm{O}}_2\to {\mathrm{O}}_2{\bullet }^{-}$$

(6)

$${\mathrm{O}}_2{\bullet }^{-}+{\mathrm{H}}_2\mathrm{O}\to \mathrm{OH}+{\mathrm{HO}}_2\bullet +{\mathrm{H}}_2{\mathrm{O}}_2$$

(7)

$${\mathrm{h}}^{+}+{\mathrm{H}}_2\mathrm{O}/{\mathrm{OH}}^{-}\to \bullet \mathrm{OH}+{\mathrm{H}}^{+}$$

(8)

$${\mathrm{h}}^{+}\mathrm{or}\bullet \mathrm{OH}+\mathrm{MB}\to \mathrm{degradation}\mathrm{products}$$

(9)

Hence, due to the synergistic effects between CaTiO₃ and geopolymer, the coupling of CaTiO₃ with geopolymer material possesses the following advantages: (i) The large specific surface area and mesoporous structure benefit the inward penetration of MB solution via pore channels, and more active sites are exposed for adsorption and photodegradation; (ii) Compared to solely photocatalytic material, the buffering of OH⁻ not only favors the adsorption via electrostatic attraction but also promotes the oxidation of MB dye by enhancing the formation of hydroxyl radicals [40].

3. Materials and Methods

3.1. Raw Materials

The TBBFS, kaolin, fumed silica (SiO₂ > 98.0 wt.%), sodium hydroxide (NaOH), cetyltrimethylammonium bromide (CTAB), hydrogen peroxide (H₂O₂), and methylene blue (MB) were used as raw materials and reagents. The chemical compositions of TBBFS and kaolin were measured by X-ray fluorescence (XRF, Panalytical Axios, Holland); the results are shown in

Table 7. Chemical composition (wt.%) of TBBFS and kaolin.

Component	CaO	SiO2	MgO	Al2O3	TiO2	Fe2O3	MnO
TBBFS	26.13	25.01	8.76	12.94	24.42	2.00	0.65
Kaolin	1.28	52.51	0.12	45.50	0.00	0.59	0.00

. The as-received TBBFS has a relatively high content of TiO₂ and a basicity (mass ratio of CaO/SiO₂) of 1.04. Considering its low available Si and Al content, the supplementary Si and Al sources, such as fumed silica and kaolin, were incorporated during the geopolymerization. Thermally activated kaolin was prepared by heating kaolin at 750 °C for 3 h.

3.2. Experimental Methods

Figure 11 schematically illustrates the synthetic route of porous geopolymer. The process consisted of steps involved in thermal modifications, alkali activation, pore-forming, and curing.

3.2.1. Thermal Treatment of TBBFS

TBBFS was ball milled (XQM-1L, Tianchuang, Changsha, China) and then placed in a tube furnace for heating to a molten state (1550 °C). After being completely melted, the molten slag was transferred to a preheated furnace to initiate the crystallization of the perovskite phase for a duration at the desired temperature. Followed by this, water quenching was performed. The obtained slag was crushed and ground into fine powders (<0.15 mm). The modified slag of S–1400 °C–1.0 h represented TBBFS underwent selective crystallization at the conditions of 1400 °C, 1.0 h of duration. In addition to selective crystallization, natural cooling and water quenching were adopted. Water-quenched slag (S-W) was prepared by directly pouring the molten slag into water (15 ± 5 °C). Natural-cooled slag (S–N) was prepared by cooling the molten slag in a furnace at a relatively slow rate (7–8 h).

3.2.2. Synthesis of Porous Geopolymer

The porous geopolymers were synthesized via alkali activation, pore-forming, and curing. The mole ratio of Si:Al:Na in the precursor was adjusted to 2:1:1. As presented in

Table 8. Process parameters for the porous geopolymers synthesis.

Material	Raw Material	Slag Proportion (wt.%)	n(H2O)/n(Na)	H2O2 Addition Amount (wt. %)
M-12H/N-0.50P-3%H2O2	S–1400 °C–1.0 h	0.50	12	3
M-16H/N-0.50P-1%H2O2	S–1400 °C–1.0 h	0.50	16	1
M-16H/N-0.50P-3%H2O2	S–1400 °C–1.0 h	0.50	16	3
M-16H/N-0.50P-5%H2O2	S–1400 °C–1.0 h	0.50	16	5
M-20H/N-0.50P-3%H2O2	S–1400 °C–1.0 h	0.50	20	3
M-20H/N-0.25P-3%H2O2	S–1400 °C–1.0 h	0.25	20	3
M-20H/N-0.75P-3%H2O2	S–1400 °C–1.0 h	0.75	20	3
W-20H/N-0.50P-3%H2O2	S–W	0.50	20	3
N-20H/N-0.50P-3%H2O2	S–N	0.50	20	3

, the effects of slag proportion, the mole ratio of H₂O/Na, H₂O₂ addition amount, and raw material were studied. In the process of alkali activation, 3 wt.% CTAB was added into the NaOH solution and stirred in a water bath until completely dissolved. Then, modified slag powders, fumed silica, and metakaolin were added into the solution and were mechanically agitated for 10 min to ensure a uniform slurry. A certain amount of H₂O₂ was added to the slurry drop-wise, along with continuous stirring, for pore formation. The slurry was cast in an 8 × 8 × 8 cm³ plastic mold and cured in a sealed bag at room temperature for 48 h, and then another 48 h in an oven at 60 °C. After curing, the porous geopolymer was ground into powders for characterization and tests.

3.2.3. Synthesis of Pure CaTiO₃

Powder mixtures were prepared by weighing, and mixing CaO and TiO₂ chemicals based on the stoichiometric ratio of CaTiO₃. The mixtures were dried and then pressed into pellets under a pressure of 30 MPa. The pellets were put into a tube furnace and calcined at 1400 °C for 3 h to synthesize pure CaTiO₃.

3.3. Adsorption and Photocatalytic Degradation Tests

MB solution of 200 mL, with a concentration of 20 mg/L, was used as a representative organic dye to evaluate the adsorption and photocatalytic properties of the porous geopolymers. The adsorption tests were performed in a glass reactor equipped with a magnetic stir and a thermostat in the dark. Sampling was conducted at certain intervals. Table S2 shows the summary of the experimental design for adsorption tests. The adsorption can be regarded as being in equilibrium once the MB concentration no longer changed. Then, the photocatalytic degradation tests were carried out under visible light irradiation with a 300 W Xenon lamp (PLS-SXE300, Perfect Light, Beijing, China). The sampling was conducted with a time interval of 10 min, and the suspension was separated by centrifugation. The residual MB concentration was measured with an ultraviolet-visible (UV-Vis) spectrophotometer (TU-1810, Puxi, Beijing, China) at a wavelength of 660 nm.

The adsorption capacity toward MB is measured from the following Equation (10):

$$Q_t=\frac{\left(C_0-C_t\right)\times V}{m}$$

(10)

where Q_t is the amount of MB dye uptake per unit mass of absorbent at time t, mg/g; C₀ and C_t represent the initial and residual concentrations of MB after time t, respectively, mg/L; V represents the volume of the solution, mL; m is the mass of the adsorbent, mg.

3.4. Characterization

The reactivity of modified slags in terms of Si, Al, and Ca dissolution was characterized by immersing slag powders in a 6 mol/L NaOH solution with a solid-to-liquid mass ratio of 1:40 at room temperature. The dissolved Si, Al, and Ca concentrations in the leachate were measured through the inductively coupled plasma–atomic emission spectrometry (ICP-AES) technique (Agilent 5100, Agilent Technologies, Los Angeles, CA, USA).

X-ray diffraction (XRD, Ultima IV, Rigaku, Tokyo, Japan, Cu radiation) was performed to determine the crystalline phases at a scanning rate of 20°/min from 10° to 90°. The scanning electron microscope (SEM, SU-5000, HITACHI, Tokyo, Japan) and energy dispersive spectrometer (EDS, X-MAX, Oxford, Oxford, UK) was used to observe the morphologies and analyzed the contents of elements in the micro-areas. The Brunauer–Emmett–Teller (BET, TriStar II 3020, Micromeritics, GA, USA) surface aera was analyzed using N₂ as the adsorption gas, degassed at 300 °C for 8 h. In addition, the mesopore size distribution was calculated from the adsorption branch of isotherm by the Barrett–Joyner–Halenda (BJH) model. The UV–Vis diffuse reflectance spectrum (UV–Vis–DRS, Lambda 950, PerkinElmer, MA, USA) was measured using BaSO₄ as reference material. Fourier transform infrared spectrometer (FTIR, Nicolet-is 10, Thermo Fisher, MA, USA) was measured to obtain chemical bonds and function group information.

4. Conclusions

The utilization of metallurgical wastes and effective activation as porous geopolymers is of great significance. In this work, TBBFS was thermally modified and then utilized as a precursor for porous geopolymers. The properties and performance of the resulting geopolymer in terms of adsorptive–photocatalytic activity towards MB removal can be greatly varied by the processing parameters. The results enable the following conclusions to be reached.

• TBBFS subjected to water quenching (fast cooling) was amorphous and resulted in the highest S_BET in the derived geopolymer, which exhibited the highest MB adsorption capacity of 97.18 mg/g.
• The adsorption process could be explained by a pseudo-second-order kinetic model and a Langmuir adsorption isotherm model. The adsorption results showed that the removal of MB was a spontaneous, exothermic, monolayer chemisorption process. Therefore, it was significantly affected by the specific surface area of the adsorbent.
• Selective crystallization of TBBFS at 1400 °C for 1 h gave the resulting geopolymer photocatalytic activity. The release of OH^- from geopolymer promotes both adsorption and photocatalytic degradation performances. The maximum removal rate for MB can reach 93.5% in 180 min. The n(H₂O)/n(Na), the addition of H₂O₂, and the use of modified slag had a positive effect on the improvement of photocatalytic activity.

The present study demonstrated that the properties and performances of geopolymers can be optimized by controlling slag chemistry. Porous geopolymer prepared from TBBFS had excellent adsorption and photodegradation performance. It provides a new way for the utilization of TBBFS in environmental purification under visible light.