Rapid Microwave-Assisted Synthesis of Fe₃O₄/SiO₂/TiO₂ Core-2-Layer-Shell Nanocomposite for Photocatalytic Degradation of Ciprofloxacin

Abstract

In this work, magnetic nanoparticles based on magnetite were successfully prepared via rapid microwave-assisted synthesis. In order to obtain the ternary core–shell Fe₃O₄/SiO₂/TiO₂ nanocomposite, first magnetite (Fe₃O₄) nanoparticles were coated with a protective layer of silica (SiO₂) and finally with titania (TiO₂). The composite configuration comprising porous and photoactive shells should facilitate the removal of organic micropollutants (OMPs) from water. Furthermore, the magnetic core is critical for processing the management of the photocatalytic powder suspension. The magnetization of the prepared magnetic nanoparticles was confirmed by vibrating-sample magnetometry (VSM), while the structure and morphology of the core–shell nanocomposite were investigated by means of XRD, FTIR, and SEM. Adsorption and photocatalysis were evaluated by investigating the removal efficiency of ciprofloxacin (CIP) as a model OMP using the prepared magnetic core–shell nanocomposite under UV-A light irradiation. It was found that the Fe₃O₄/SiO₂/TiO₂ nanocomposite showed good synergistic adsorption and photocatalytic properties. The measurement of iron in eluate confirmed that no leaching occurred during the photocatalytic examination. The recovery of magnetic nanocomposite by an external magnetic field confirmed that the magnetically separated catalyst is highly suitable for recycling and reuse.

1. Introduction

Magnetic nanomaterials have been getting a lot of attention lately due to their specific physical properties and various applications in medicine and biomedicine. Another important application lies in the area of supports for photocatalysts in advanced oxidation processes for the degradation of organic micropollutants (OMPs).

Due to their various applications and specific physical properties, magnetic nanomaterials are a constant topic of scientific research. Magnetic properties of materials change significantly, when the size of each particle is reduced to nanoscale compared to those of bulk materials [1]. Therefore, by having uniformly seized magnetic nanoparticles (such as magnetite), one can enable a facile separation process, i.e., extraction of the magnetic nanoparticles from a solution using an external magnetic field. Magnetite is one of the most famous iron oxides with inverse spinel structure B(AB)O₄. A and B ions in parentheses occupy octahedral sites, while the rest of the B ions occupy tetrahedral sites [2]; thus, magnetite shows ferrimagnetic ordering. However, when the size of each particle is reduced to nanoscale, precisely between 15 and 20 nm, the particles will exhibit magnetic moment as a single domain under an external magnetic field which behaves as a superparamagnet [3], whereas in the absence of a magnetic field they will have zero average residual magnetization, and more precisely, their magnetization disappears [4]. In that case, magnetic behavior is determined by the magnetic anisotropy energy of each particle and the magnetic dipole–dipole interaction between the particles. For the particle to exhibit superparamagnetic behavior, the magnetic anisotropy energy must be greater than that of the dipole–dipole interaction [1]. This behavior allows the fast, easy, reversible and selective magnetic separation of the particles from a solution using an external magnetic field. The use of magnetite nanoparticles is advantageous because of their non-toxicity and low cost compared to other magnetic nanoparticles such as nickel and cobalt [5,6]. Consequently, magnetite nanoparticles have found applications such as drug delivery systems [7], magnetic imaging [8], magnetic resonance imaging (MRI) [9], magnetic hyperthermia applications [10], heavy metal detection [11], lithium-ion batteries [12], and antibacterial activities [13]. Photocatalytically, magnetic nanoparticles have been used in various configurations such as supports of photocatalysts for the photodegradation of various dyes [14,15,16,17,18], natural organic matter in water [19], herbicides in wastewater [20], the treatment of drinking water [21], and the removal of pharmaceuticals [22,23,24].

Magnetic nanoparticles can be synthesized using various physical methods such as gas-phase deposition, electron beam lithography, pulsed laser ablation, laser-induced pyrolysis, power ball milling, combustion, and chemical methods including co-precipitation, thermal decomposition, reverse microemulsion, and hydrothermal, solvothermal, and lately microwave-assisted synthesis [3]. Each of the abovementioned methods shows some limitations in either complexity, modularity, processing price, or yield homogeneity, while comparatively the microwave-assisted synthesis may offer a simple, variable, cheap and fast alternative synthetic route. The microwave-assisted synthesis is based upon the interaction of microwaves with the material, and more precisely, molecules with a dipole moment absorb microwaves and thereby transform energy to heat which is generated within the material or suspension itself. The temperature gradient in microwave synthesis is therefore opposite to that in conventional heating, i.e., from the inside out, the so-called in-core heating. Microwave heat transfer depends on the specific loss factor characteristic for each solvent. The higher this value, the better the solvent will absorb microwaves [25,26]. During synthesis, high energy output enables high heating rates and high product yields, but also a precise heating control, all of which enable rapid phase formation with a monodisperse particle size distribution [27,28]. Shorter synthesis time is also enabled by the superheating phenomenon, in which the solvent when exposed to microwaves in a closed reactor can be heated to temperatures above the atmospheric boiling point without boiling [29].

Magnetite nanoparticles are not particularly photoactive; therefore, for their use in advanced oxidation processes (AOPs), a photocatalytic semiconductor is necessary. Due to its superior photocatalytic activity, low price, good chemical stability, and non-toxicity, TiO₂ is one of the most common and well-known semiconductors. Chemical reactions on a TiO₂ surface are induced by the absorption of photons from a light source, with a wavelength below 400 nm. The absorption of light causes the promotion of electron (e⁻) from the valence band to the conduction band, which generates a hole (h⁺) in the valence band of the photocatalyst. Photocatalytic activity can be further improved by adding various electron scavengers, which react with electrons and prevent the recombination of electron–hole pairs, thus enabling the formation of different radicals which degrade pollutants [30]. Balayeva et al. [31] and Yu et al. [32] developed a new visible-light-sensitive photocatalyst based on TiO₂. TiO₂ as a photocatalyst can be used in the form of TiO₂ powder suspension, or it can be immobilized by different techniques on various substrates [29,33,34]. The main problem of photocatalyst application in the form of a suspension is their separation from the treated water [35]. One way of the immobilization of TiO₂ is the deposition of the TiO₂ shell on the magnetite core, which allows the separation of the photocatalyst by an external magnet from the treated water. A sol-gel route is an established chemical route that can be easily utilized for the deposition of titania [29]. A similar sol-gel process can be used to derive another shell layer [14], in this case a protective silica shell layer. It has been reported that, in the case of the direct contact between iron oxide and TiO₂, an electron transfer from titania to iron oxide occurs which causes phase separation and consequently the leaching of iron [12,28]. In order to prevent the unwanted iron leaching, inserting a buffer-protective silica shell layer between the magnetite core and the outer titania shell should mitigate the mentioned electron transfer.

Some photocatalysts have also shown favorable adsorption behavior in addition to photocatalytic degradation performance, for example in the case of rhodamine dye degradation by BiVO₄ [36], remazol brilliant blue dye by N-TiO₂ [37], methylene blue by the ternary MgFe₂O₄–TiO₂[email protected] nanocomposite [38], ciprofloxacin (CIP) by the ternary BiOCl/CQDs/rGO photocatalyst [39], and methyl orange by nano-heterostructure [email protected] [40]. According to the available literature, the adsorption and photocatalytic behavior of the core–shell Fe₃O₄/SiO₂/TiO₂ nanocomposite, with respect to the possible synergistic performance, has not been investigated so far. Therefore, in the present work, the microwave-assisted synthesis, characterization, adsorption, and photocatalytic properties of this core–shell nanocomposite were studied. CIP was used as a model micropollutant from the class of quinolone antibiotics. The degradation data were fitted with kinetic models to explain the mechanism of adsorption.

2. Results and Discussion

2.1. Characterisation of Core–Shell Fe₃O₄/SiO₂/TiO₂ Nanoparticles

Figure 1 shows the FTIR spectra for Fe₃O₄, Fe₃O₄/SiO₂, and Fe₃O₄/SiO₂/TiO₂ nanoparticles synthesized at 100 °C (Figure 1a), 150 °C (Figure 1b), and 200 °C (Figure 1c) by the microwave-assisted method. Additionally, Figure 1d shows the FTIR spectra of pure TiO₂ and SiO₂ as a reference.

The main band for magnetite nanoparticles was observed at around 550 cm⁻¹ and was assigned to the Fe–O stretching vibration [1]. The FTIR spectra of Fe₃O₄/SiO₂ particles showed an absorption band around 1100 cm⁻¹, which was assigned to the Si–O–Si asymmetric stretching vibration. The band around 800 cm⁻¹ originated from the deformation vibration of Si–O bonds [30], while the band at 950 cm⁻¹ was assigned to the asymmetric bending and stretching vibration of Si–OH [41]. The Fe₃O₄/SiO₂/TiO₂ FTIR spectra showed several bands. The band around 400–450 cm⁻¹ was due to the stretching vibration of Ti–O–Ti [42]. The absorption bands in the range of 2800–3800 cm⁻¹ were due to the stretching vibrations of OH groups, probably from adsorbed water but could also be from the OH groups bonded to Si and Ti (Ti–OH and Si–OH). A small peak was observed around 960 cm⁻¹ and was assigned to the Si–O–Ti stretching vibration, which indicated a bond between silica and titania layers [18]. The changing of the synthesis temperature barely affected the vibration spectra of the obtained nanoparticles. Characteristic Ti–O–Ti and Si–O bands observed on the FTIR spectra of Fe₃O₄/SiO₂ and Fe₃O₄/SiO₂/TiO₂ nanoparticles corresponded to those of pure SiO₂ and TiO₂.

The XRD analysis (Figure 2a–c) showed magnetite (Fe₃O₄) (ICDD PDF#19-0629) as the main crystalline phase in all samples (synthesized by the microwave-assisted method at 100, 150, and 200 °C). The samples thermally treated at lower temperatures (100 °C) also showed barely noticeable traces of goethite (FeO(OH); ICDD PDF#29-0713; highlighted with pink squares) (Figure 2a). There were no amorphous iron oxide phases or unassigned peaks. For samples with a silica coating (Figure 2b), no characteristic patterns of silica crystalline phases were observed; however, a hump centered around 2θ of 26° characteristic of amorphous silica was evidenced, confirming the presence of the SiO₂ phase (highlighted with yellow squares). As a consequence of the silica coating, the intensity of the diffraction signal from the magnetite phase was only slightly reduced, as the magnetite core was less available to X-rays, thereby proving the core–shell configuration of the sample. There were no additional silica amorphous phases or unassigned peaks. In the sample additionally coated with TiO₂, anatase was observed as the main phase (ICDD PDF#21-1272), magnetite is the minor phase, and the silica hump was barely visible (Figure 2c). In this case, the reduction of the diffraction signal from the magnetite phase also pointed out to the magnetite core, which was less exposed to X-rays, to the middle silica shell, which was intermediately exposed to X-rays, and the outer titania shell, readily exposed to X-rays. There were no titania amorphous phase or unassigned peaks. The synthesis temperature showed no effect on the obtained nanoparticles.

Diffraction results are in agreement with the FTIR results and confirmed the successful synthesis of the Fe₃O₄/SiO₂/TiO₂ nanocomposites but additionally pointed out a two-layer core–shell configuration.

The magnetization measurements were conducted at room temperature and are shown in Figure 3. The magnetization curves showed that the obtained particles exhibited superparamagnetic behavior. The values of saturation magnetization amounted to 59, 35, and 17 emu g⁻¹ for Fe₃O_4, Fe₃O₄/SiO₂, and Fe₃O₄/SiO₂/TiO₂ nanoparticles, respectively. The addition of SiO₂ and TiO₂ layers reduced the saturation magnetization; however, it was still enough to remove the particles from the suspension by an external magnetic field. The samples synthesized at 100 °C showed the highest values of saturation magnetization and were thus chosen for further photocatalytic experiments.

The texture and morphology of the core–shell nanocomposites were investigated using SEM analysis with different magnifications, shown in Figure 4. The magnetite nanoparticles, shown in Figure 4a–c, had a disordered surface texture. The presence of agglomerates was due to the small size of particles and their magnetization. The surface displayed rather low surface roughness compared to the particles coated with a layer of SiO₂, shown in Figure 4d–f. The SiO₂ layer seemed to have another role in the process of manufacturing the nanocomposites, and it controlled the particle size and shape, which can be seen in the form of regularly shaped round particles in Figure 4d. The round particles were obtained with the synthesis temperature of 100 °C. The Fe₃O₄/SiO₂/TiO₂ nanocomposite seemed to have a porous microstructure, which can enhance photocatalytic efficiency. However, the presence of agglomerates might reduce the active surface. To address agglomeration issues, the use of a surfactant and a longer microwave irradiation with high stirring rates may be beneficial [43,44,45].

2.2. Synergetic Effects of Adsorption and Photocatalysis

2.2.1. Adsorption Kinetic Studies

Prior to the photocatalytic degradation of CIP in an aqueous solution, adsorption tests were conducted to evaluate the adsorption kinetics [39,40]. The obtained results after 120 min of stirring in the dark with the synthesized photocatalyst are shown in Figure 5. The percentage of adsorption efficiency of the Fe₃O₄/SiO₂/TiO₂ nanocomposite was calculated using the equation:

$$\eta , \%=\frac{C_0-C_t}{C_0}\times 100,$$

(1)

where η is the percentage of adsorption efficiency, C₀ (mg dm⁻³) is the initial CIP concentration before adsorption, and C_t (mg dm⁻³) is the concentration of CIP at time t (min) of adsorption. It can be seen that the adsorption/desorption equilibrium was established within 30 min, with 56% of CIP adsorbed on the photocatalyst surface. Therefore, the adsorption process kinetics and mechanisms were analyzed.

In order to yield further information about the mechanisms involved, the adsorption kinetics data were fitted with several model equations presented in the following sections, namely the Lagergren pseudo-first-order model and Ho’s pseudo-second-order kinetic model, the Weber–Morris intraparticle diffusion, and the Boyd plot film diffusion models [46].

The kinetics of the CIP adsorption was investigated by applying pseudo-first-order and pseudo-second-order models. The Lagergren pseudo-first-order model is described by the following equation [47]:

$$\frac{d{q}_t}{dt}=k_1(q_e-q_t),$$

(2)

where q_e and q_t are the amounts of CIP (mg g^–1) adsorbed on the Fe₃O₄/SiO₂/TiO₂ nanocomposite at equilibrium and at time t, respectively, while k₁ (min⁻¹) is the rate constant of the pseudo-first-order sorption. Upon integrating with the initial conditions of q = 0 when t = 0, Equation (3) yields:

$$q=q_e\left(1-\exp \left(-kt\right)\right).$$

(3)

Its linearized form is written as:

$$\ln \left(q_e-q_t\right)=\ln q_e-k_{1}t.$$

(4)

The plotting (Figure 6a) of ln(q_e − q_t) against t gave q_e = exp(intercept) and k₁ = −(slope).

The kinetic data were further analyzed using Ho’s pseudo-second-order kinetic model. This model assumes that the uptake rate is second-order with respect to the available surface sites [48]. The pseudo-second-order equation [49] is represented as:

$$\frac{d{q}_t}{dt}=k_2{(q_e-q_t)}^2,$$

(5)

where q_e and q_t are the amounts of CIP (mg g⁻¹) adsorbed on the Fe₃O₄/SiO₂/TiO₂ nanocomposite at equilibrium and at time t, respectively, while k₂ is the rate constant of pseudo-second-order adsorption (mg g⁻¹ min⁻¹). Integrating Equation (5) with the initial conditions of q = 0 when t = 0 and subsequent rearrangement obtains the linearized form:

$$\frac{t}{q_t}=\frac{1}{k_2{q}_e^2}+\frac{t}{q_e}.$$

(6)

A plot (Figure 6b) of t/q_t against t gave 1/q_e as the slope and $1/k_2{q}_e^2$ as the intercept. The values of q_e, k₁, and R² obtained after the linear plots of Equation (4) and q_e, k₂, and R² from the plots of Equation (6) for the CIP adsorption on the ternary core/shell Fe₃O₄/SiO₂/TiO₂ nanocomposite are reported in

Table 1. The pseudo-first-order and pseudo-second-order sorption models constants of CIP on the ternary core–shell Fe₃O₄/SiO₂/TiO₂ nanocomposite.

qe,exp (mg g−1)	Kinetic Model
	Pseudo-First-Order			Pseudo-Second-Order
	k1 (min−1)	qe,cal (mg g−1)	R2	k2 (g mg−1 min−1)	qe,cal (mg g−1)	R2
10.91	0.0476	1.83	0.9772	0.107	10.72	0.9998

.

It can be seen (Table 1) that for a pseudo-first-order model, the linear correlation coefficient (R²) was lower than the pseudo-second-order correlation coefficient (R²). The correlation coefficients for the pseudo-second-order kinetic model was very high (R² > 0.99), and the theoretical q_e,cal values were closer to the experimental q_e,exp values at the studied initial CIP concentration. This suggests that the adsorption of CIP on the ternary core/shell Fe₃O₄/SiO₂/TiO₂ nanocomposite might be controlled by the second-order model.

2.2.2. Sorption Mechanism—Intraparticle Diffusion Model

The two kinetic models listed above could not definitely reveal the adsorption mechanism as well as the rate controlling steps in the sorption process. Thus, the intraparticle diffusion model according to Weber and Morris [50] was further applied in the present study. The intraparticle diffusion equation is expressed as:

$$q_t=k_{\mathrm{pi}}\sqrt{t}+C_i,$$

(7)

where k_pi (mg g⁻¹ min^1/2) is the rate parameter of stage I and is obtained from the slope of the straight line of q_t versus t^1/2; C_i, the intercept of stage i, gives an idea about the thickness of boundary layer, i.e., the larger the intercept, the greater the boundary layer effect. If intraparticle diffusion occurs, then q_t versus t^1/2 will be linear, and if the plot passes through the origin, then the rate limiting process is only due to the intraparticle diffusion. Otherwise, some other mechanism along with intraparticle diffusion is also involved. For an adsorbate/adsorbent adsorption process, the adsorbate transfer may include the step of either external mass transfer (film diffusion) or intraparticle diffusion, or both. The intraparticle diffusion plots of q_t against t^1/2 (Figure 7a) consisted of three linear sections with different multi-linear sections, including three linear sections with different slopes, which indicates that multiple steps take place during the sorption process [51].

The first stage of sorption (the section of the curve with a large slope) corresponds to the transport of adsorbate, CIP from the bulk solution to the external surface of adsorbent, and ternary Fe₃O₄/SiO₂/TiO₂ nanocomposite by film diffusion, which is also called outer diffusion (or boundary layer diffusion). The second stage of sorption describes the gradual adsorption stage, corresponding to the diffusion of the adsorbate, the ternary core–shell Fe₃O₄/SiO₂/TiO₂ nanocomposite from the external surface into the pores of the adsorbent, and the ternary Fe₃O₄/SiO₂/TiO₂ nanocomposite, which is called intraparticle diffusion or inner diffusion.

The third stage with a small slope indicates the final equilibrium stage. This step is considered very fast and thus cannot be treated as the rate-controlling step. Generally, the adsorption rate is controlled by outer diffusion or intra-particle diffusion or both. It is clear that the rate-controlling step of CIP adsorption on the ternary core–shell Fe₃O₄/SiO₂/TiO₂ nanocomposite involves complex processes, including outer diffusion (film diffusion) and intraparticle diffusion. The model parameters obtained from the three stages of plots are listed in

Table 2. Intraparticle diffusion model constants and correlation coefficients for the adsorption of CIP on the ternary Fe₃O₄/SiO₂/TiO₂ nanocomposite.

Intraparticle Diffusion
First Stage of Sorption			Second Stage of Sorption			Third Stage of Sorption
kp1 (mg g−1 min−1/2)	C1	R2	kp2 (mg g−1 min−1/2)	C2	R2	kp3 (mg g−1 min−1/2)	C3	R2
0.458	8.34	0.9895	0.186	9.37	0.9703	0.0486	10.46	0.9976

.

Based on Table 2, the curves do not cross the origin, because the charts do not cut the zero point, so the intraparticle diffusion is not the only rate-limiting stage in this adsorption system and other mechanisms are also included. To better understand the principal mechanism for controlling the rate of the adsorption process, the Boyd diagram was used with the utilization of the following equation and the drawing of the B_t graph in terms of t. The role of controlling the rate of film diffusion and intraparticle diffusion in the mechanism of adsorption of CIP can be determined by plotting this diagram. Thus, if the linear plot of data fitting has an intercept of zero and the regression coefficient is also higher than 0.99, the intraparticle diffusion of the process stage will control the process speed; otherwise, the influence of the film will also be involved. As shown in Figure 7b, this diagram is linear but does not cross the origin, bringing to the conclusion that the inherent penetration along with the film penetration governs the adsorption.

2.2.3. Photocatalytic Kinetic Studies

Comparisons of results of dark adsorption [52], photolysis, and photocatalytic degradation (three replicates) of CIP are presented in Figure 8. It can be seen that the photolytic (without photocatalyst nanocomposite) degradation of CIP lowered its concentration by around 40% and dark adsorption by around 56% after 30 min, while photocatalytic degradation lowered CIP concentration by around 94% after 120 min of irradiation.

The efficiency of photocatalytic degradation (η; %) of CIP by the Fe₃O₄/SiO₂/TiO₂ nanocomposite synthesized at 100 °C is shown in Figure 9a. The efficiency of photocatalytic degradation was calculated according to Equation (1). It can be seen that the degradation efficiency was 94.0% after 120 min of photocatalysis under UV light.

In order to investigate the kinetics of the photocatalytic degradation of CIP by the Fe₃O₄/SiO₂/TiO₂ nanocomposite, the pseudo-first-order and pseudo-second-order kinetic models were used. The linear form of the pseudo-first-order kinetic model is described as [53]:

$$ln\frac{C_0}{C_t}=k_1·t.$$

(8)

The linear form of the pseudo-second-order kinetic model is written as [53]:

$$\frac{1}{C_t}-\frac{1}{C_0}=k_2·t,$$

(9)

where C_t (mg dm⁻³) is the concentration of CIP at time t (min), C₀ (mg dm⁻³) is the initial CIP concentration, and k₁ (min⁻¹) and k₂ (mg dm⁻³ min⁻¹) are the degradation rate constants.

The first-order degradation rate constant (k₁) from Equation (8) can be calculated by the slope of the straight line obtained by plotting the linear regression of −ln(C/C₀) versus irradiation time (t) (Figure 9b). The second-order degradation rate constant (k₂) from Equation (9) can be calculated by the slope of the straight line obtained from plotting linear regression of $\frac{1}{C_t}-\frac{1}{C_0}$ versus irradiation time (t) (Figure 9c). The degradation rate constants k₁ and k₂ were as follows: 0.0158 min⁻¹ and 0.0281 mg dm⁻³ min⁻¹. It can be seen (Figure 9a,b) that for a pseudo-first-order model, the linear correlation coefficient (R²) was lower (0.9195) than the pseudo-second-order correlation coefficient (0.9871). According to the obtained data, the photocatalytic degradation of CIP by the ternary core/shell Fe₃O₄/SiO₂/TiO₂ nanocomposite was best fitted with pseudo-second-order kinetics.

2.3. Reusability and Stability of the Magnetic Ternary Core–Shell Fe₃O₄/SiO₂/TiO₂ Catalyst

Reusability and stability is vital for the catalyst and was confirmed by repeating the decomposition process three times (Figure 10). After three repetitions (photocatalytic degradation of three cycles), the photodegradation efficiency of CIP decreased from 94.0 (1st cycle) to 91.0% (3rd cycle). Between cycles, the magnetic nanocomposite was removed from the solution by an external magnetic field, washed and dried. The magnetic ternary core–shell Fe₃O₄/SiO₂/TiO₂ catalyst featured high stability and suitable reusability under UV light irradiation.

The measurements of iron concentration in eluate after adsorption, photolysis, and photocatalysis tests were performed by means of atomic absorption spectroscopy and confirmed that no iron leaching occurred during the photocatalytic examination.

3. Materials and Methods

3.1. Materials

For the synthesis of magnetic nanoparticles (Fe₃O₄), iron(III) chloride hexahydrate (FeCl₃·6H₂O; VWR chemicals, Germany), iron(II) sulfate heptahydrate (FeSO₄·7H₂O; Alfa Aesar, Kandel, Germany), sodium hydroxide (NaOH; Grammol, Zagreb, Croatia), and deionized water (DI) were used.

For the SiO₂ coating, SiO₂ sol was prepared by mixing ethanol (EtOH, 96% p.a.; Grammol, Croatia) as the solvent and tetraethoxy silane (TEOS; Merck, Darmstadt, Germany) was used as the precursor, while ammonia (NH₃, 25%; Grammol, Zagreb, Croatia) was used as the catalyst.

For the TiO₂ coating, TiO₂ sol was prepared by mixing titanium(IV) isopropoxide TIP (Sigma-Aldrich, St. Louis, MO, USA) as the precursor, 2-propanol (PrOH; Grammol, Croatia) was used as the solvent, acetylacetone (AcAc; Sigma-Aldrich, St. Louis, MO, USA) was utilized as the chelating agent, and nitric acid (HNO₃; Carlo Erba Reagents, Barcelona, Spain) was employed as the catalyst.

For photocatalytic experiments CIP (98%; Acros organics, Thermo Fisher Scientific, NJ, USA) was used as the model OMP.

3.2. Microwave-Assisted Synthesis of Magnetic Nanoparticles

Aqueous solutions of FeCl₃·6H₂O (0.4 M) and FeSO₄·7H₂O (0.2 M) were mixed together, after which a water solution of 2 M NaOH was added. The stirring was kept constant for 15 min. The solution was afterwards placed in a microwave oven (Anton Paar monowave 600, Graz, Austria) and irradiated at 100, 150, and 200 °C for 5 min under stirring. The obtained dark precipitates (Fe₃O₄) was separated from the suspensions by a magnet, washed several times with DI and dried at 80 °C for 2 h.

3.3. Synthesis of Fe₃O₄/SiO₂ Nanoparticles

Half a gram of dried magnetite particles were dispersed in a solution of ethanol, DI, and ammonia. The suspension was ultrasonicated for 15 min. After ultrasonication, TEOS was added dropwise to the solution with magnetite and stirred for 24 h. The TEOS:EtOH:DI:NH₃ molar ratio of the used chemicals was 1:100:32:0.003 [27]. The obtained particles (Fe₃O₄/SiO₂) were then separated from the suspension with a magnet, washed several times with DI and dried at 40 °C for 3 h.

3.4. Microwave-Assisted Synthesis of Fe₃O₄/SiO₂/TiO₂ Nanoparticles

Half a gram of dried Fe₃O₄/SiO₂ particles were dispersed in ethanol and ultrasonicated for 15 min. TiO₂ sol was prepared by mixing Pr-OH, AcAc, TIP, and 0.5 M HNO₃ in a TIP:PrOH:AcAc:HN molar ratio of 1:35:0.63:0.015 [28] and left covered until the next day. The next day, TiO₂ sol was added dropwise to the suspension with magnetic particles under vigorous stirring. The suspension was stirred for 15 min and transferred in a microwave oven at 200 °C for 10 min. The obtained Fe₃O₄/SiO₂/TiO₂ nanocomposites were separated from the suspension with a magnet, washed several times with DI and dried at 60 °C for 3 h.

3.5. Materials Characterization

All the particles, i.e., Fe₃O₄, Fe₃O₄/SiO₂, and Fe₃O₄/SiO₂/TiO₂, were characterized via vibrating-sample magnetometry (VSM), FTIR, XRD, and SEM.

VSM was performed using a Lake Shore Cryotronics vibrating sample magnetometer (Westerville, OH, USA). Hysteresis measurements were conducted in continuous acquisition mode with the maximum field of 20 kOe and a step size of 20 Oe.

FTIR measurements were performed using IRSpirit (Shimadzu, Tokyo, Japan) equipped with the single-reflection attenuated total reflectance (ATR) accessory in the wavenumber range of 400 to 4000 cm⁻¹.

XRD was performed on XRD-6000 (Shimadzu, Tokyo, Japan) using CuKα radiation at an accelerating voltage of 40 kV and a current of 30 mA. All samples were analyzed in a 2θ range of 5°–75° in a continuous mode with a 0.02° 2θ step and a scan rate of 0.6 s.

SEM was conducted via SEM Tescan Vega III Easyprobe, with an accelerating voltage of 10 kV, equipped with secondary (SE) and backscattered electron (BSE) detectors (Tescan, Brno, Czech Republic).

3.6. Synergetic Adsorption and Photocatalytic Evaluation

The photocatalytic activity of the prepared magnetite-based magnetic nanocomposite synthesized at 100 °C was examined by the degradation of CIP as the selected micropollutant. Fifty milligrams of the photocatalyst were dispersed in a 100 cm³ aqueous CIP solution, with a concentration of 10 mg dm⁻³ irradiated by UV-A (365 nm) lamp (model UVAHAND LED; Dr. Hönle AG, München, Germany). The photocatalysis process was carried out in a round reactor made of borosilicate glass with a flat bottom, shown in Figure 11. The selected lamp was placed under the reactor at a distance of 10 cm, while stirring was provided from above with a polyamide stirring bar.

Before photocatalytic evaluation, adsorption tests were conducted by stirring 100 cm³ of the aqueous CIP solution with the photocatalyst in the dark for 120 min. Based on the obtained results, the adsorption kinetics was evaluated.

The photolysis effect was also evaluated by stirring 100 cm³ of the aqueous CIP solution for 120 min, while the solution was irradiated with a lamp without the photocatalyst in the reactor.

CIP degradation was followed as an absorbance decrease by UV/VIS spectrophotometry (Spekol 2000, Analytic Jena, Jena, Germany) at a wavelength of 273 nm. CIP can exist as a cation (pK_a lower than 5.90), a zwitterion (pK_a between 5.90 and 8.89), and an anion (pK_a above 8.89) under typical water pH conditions, as shown in Figure 12. Changing the pH values affected both the surface charge of the adsorbent and the degree of ionization. The electrostatic effects between the catalyst surface and the functional groups of the micropollutant at active sites of the catalyst were also affected by pH value. The efficiency of the catalyst at pH values lower than ~6 was reduced because of the repulsive effect between the positively charged catalyst surface and CIP. On the other hand, the efficiency at pH values higher than ~9 was reduced due to the electrostatic repulsion of negative charges of CIP and TiO₂ [54,55]. Based on all mentioned before, the pH of the CIP solution was kept at around 6.5.

4. Conclusions

Fe₃O₄/SiO₂/TiO₂ nanocomposites were successfully prepared by microwave-assisted synthesis. The FTIR and XRD analysis confirmed the successful synthesis of a magnetic nanophotocatalyst. The magnetization curves showed that the obtained particles exhibited superparamagnetic behavior. The SEM analysis showed a disordered surface texture of the prepared magnetite particles. The presence of some agglomerates occurred due to the small size of particles and their magnetization. To address agglomeration issues, the use of a surfactant and a longer microwave irradiation with high stirring rates may prove beneficial.

Adsorption kinetic studies suggested that the adsorption of CIP on ternary core–shell Fe₃O₄/SiO₂/TiO₂ nanocomposites might be controlled by the second-order model. The intraparticle diffusion plots indicated that multiple steps took place during the sorption process. The Boyd diagram showed that the inherent penetration along with the film penetration controlled the adsorption mechanism. The synergetic removal of CIP encompassed photolysis (without photocatalyst nanocomposites) degradation of around 40%, dark adsorption degradation of around 56% after 30 min, and photocatalytic degradation around 94% after 120 min of irradiation. The magnetic ternary core–shell Fe₃O₄/SiO₂/TiO₂ catalyst featured high stability and good reusability under UV light irradiation. After three replications, the photodegradation efficiency of CIP decreased from 94.0% to 91.0%. The measurement of iron concentration in eluate confirmed that no leaching occurred during the photocatalytic examination.

Efficient photocatalyst separation by an external magnetic field will allow the reuse of core–shell nanocomposites in repeating processes of water purification.