Sage Journals: Discover world-class research

Abstract

Diatomite was slightly modified with a sodium hydroxide solution. The resulting material was characterized by using energy-dispersive X-ray spectroscopy (EDX), X-ray diffraction (XRD), Fourier-transform infrared spectroscopy (FT-IR), scanning electron microscopy (SEM), and nitrogen adsorption-desorption isotherms. The so-treated diatomite has a high specific surface area (77.8 m²/g) and a high concentration of isolated silanol groups on the surface, and therefore, its adsorption capacity increases drastically in both the single and binary adsorption systems for rhodamine B and methylene blue. The binary system is more effective than the single system, with methylene blue being adsorbed more than rhodamine B. The adsorption process is spontaneous and fits well with the Langmuir isothermal model, and it depends on pH significantly.

1. Introduction

Dyes are widely used in numerous applications, such as textile, paper, plastic, and dye industries [1]. The amount of dyes produced annually worldwide is estimated at over $7 \times 10^{5}$ tons, and more than 100,000 commercially available dyes with different physical and chemical properties are being used [2–4]. Various dyes and their decomposition products are toxic and carcinogenic, thus posing a danger to aquatic organisms [1, 5]. Therefore, dye removal from wastewater is essential.

A large number of dyes have a complex aromatic ring structure and are difficult to degrade biologically [4, 6]. Therefore, it is necessary to reduce their concentration in wastewaters prior to biological treatment. Chemical oxidation has been extensively studied for dye removal from wastewaters [1, 7–9]. However, oxidation often produces intermediate products that can cause secondary pollution. Meanwhile, the adsorption technique has proven to be a simple, efficient, and attractive way to remove nonbiodegradable pollutants (including dyes) from wastewaters [5, 10, 11].

To remove dyes from complex aqueous solutions, a variety of adsorbents have been used, such as banyan aerial roots [12], peat [2], bentonite [13], mesoporous silica nanoparticles [14], clay [15, 16], activated banana peel carbon [17], silica extracted from rice husk [18], and zeolite [19], and some of them exhibit high performance. However, the search for new, effective, cheap, and environmentally friendly adsorbents is on the way.

Diatomite is a low-density, small-particle sedimentary rock consisting mainly of amorphous silica (SiO₂·nH₂O) derived from diatoms. Diatomite encompasses a variety of structures and has high porosity (up to 80%), a large specific surface area, and multiple hydroxyl groups on the surface [3, 6, 10, 11, 20]. These properties enable diatomite to be a potential adsorbent for the pollutants present in industrial wastewaters, including dyes. Besides, diatomite is abundant in nature, cheap, and environmentally friendly [11]. Several studies have dealt with the applicability of natural diatomite in the adsorption field [6, 10, 11, 21–23]. Other studies have focused on diatomite surface modification with metals or organic functional groups to improve adsorption efficiency or expand its applications [1, 7–9, 24–32]. In some studies, natural diatomite is treated thermally [3, 10, 20, 33, 34], with acids [3, 20, 35–37], or with alkalines [4, 37, 38] to enhance its application performance. Other studies use diatomite as a raw material to manufacture other products [14, 35, 39–42]. The diatomite purified by calcining is also investigated by Yuan et al. [43]. They discovered that when the temperature increases, the condensation of surface silanol groups occurs. Hydrogen-linked hydroxyl groups condense more easily than isolated hydroxyl groups. Bronsted acid centers also condense at high temperatures. This condensation reduces the adsorption capacity of the diatomite treated by calcining toward base dyes. When treated with acids (normally at high concentration: 5 M H₂SO₄ [3], 5 M HCl [35], 1-5 M HCl [36], 10% HCl [20], and 1 M H₂SO₄ [37]), it is difficult to perform the modification and is easily contaminated by secondary pollution. Therefore, numerous studies have focused only on diatomite purification because it is cheap, easy to operate, and environmentally friendly [4]. When purified with alkali, diatomite retains its hydroxyl groups on the surface, and they are excellent adsorption centers for many metals as well as dyes.

Since most industrial wastewaters contain different pollutants, it is important to investigate the effect of multicomponent systems on the adsorption capacity. Various studies have studied the simultaneous removal of different pollutants from aqueous solutions [2, 5, 44] to assess the competitiveness of adsorbates. In this study, natural diatomite is activated by treating with low-concentrated sodium hydroxide to enhance the adsorption capacity for rhodamine B (RB) and methylene blue (MB) in single and binary systems. The equilibrium isotherms and thermodynamic parameters of the adsorption processes are studied. In addition, the effect of the solution pH on the adsorption efficiency of RB or MB in the single system is also investigated.

2. Materials and Methods

2.1. Materials

Natural diatomite was obtained from Phu Yen province, Vietnam. Natural diatomite was washed several times with water, dried at 100°C, sieved, and stored in closed containers for further tests. The product is called purified diatomite.

Sodium hydroxide (NaOH), hydrochloric acid (HCl), and potassium chloride (KCl) were purchased from Guangdong (China). Methylene blue (Guangdong, China) and rhodamine B (HiMedia, India) dyes were used as adsorbates. A summary of the main characteristics of these dyes is given in Table 1 [3, 5, 22, 27, 37].

Table 1

Main characteristics of the dyes used in this study.

Dye	RB	MB
Type	Basic violet 10, C.I.45170, cationic	Basic blue 9, C.I.52015, cationic
Phase	Solid	Solid
Molecular formula	C₂₈H₃₁O₃N₂Cl	C₁₆H₁₈N₃SCl
Molecular weight (g/mol)	479.03	319.85
Chemical structure

2.2. Activation of Diatomite

Purified diatomite was activated with NaOH to enhance the adsorption capacity. The purified diatomite sample was immersed in a 5% NaOH solution at a ratio of 1 : 10 ( $w / w$ ) and stirred at 100°C for 2 h to remove impurities and organics. Then, the solid was filtered, washed several times with distilled water, dried at 100°C, and sieved. The obtained alkali-activated diatomite was stored in closed containers for further tests.

2.3. Characterization

The chemical analysis of diatomite was performed by using energy-dispersive X-ray spectroscopy (EDX, JEOL JED-2300, Japan) at different sites of the material. The powder X-ray diffraction (XRD) patterns were recorded by VNU-D8 Advance, Bruker, Germany, with Cu Kα radiation ( $λ = 1.5406 Å$ ). Fourier-transform infrared spectra (FT-IR) were measured on a Jasco FT/IR-4600 spectrometer (Japan) with a range of 4000-400 cm⁻¹. The morphology of diatomite was observed with scanning electron microscopy (SEM) using SEM JMS-5300LV (Japan). Nitrogen adsorption/desorption isotherm measurements were conducted using a TriStar 3000 analyzer. Samples were pretreated by heating at 250°C for 5 h with N₂ before the measurements.

2.4. Point of Zero Charge

The point of zero charge (pH_PZC) of the adsorbent was determined to follow the methods of Mahmood et al. [45], Jing et al. [46], and Du and Hoai [47]. To a series of 100 mL Erlenmeyer flasks, 50 mL of a 0.01 M KCl solution was added. The initial pH (pH_i) of the solutions was adjusted, ranging from 2 to 12, by adding a 0.1 M HCl or 0.1 M NaOH solution. Then, 0.1 g of the adsorbent was added to each flask and mixtures were shaken for 48 h. The final pH (pH_f) of the solutions was measured. The difference between the final and initial pHs ( $Δ pH = p H_{f} - p H_{i}$ ) was plotted against the pH_i. The point of intersection of the curve with the abscissa, at which $Δ pH = 0$ , provides pH_PZC.

2.5. Adsorption

2.5.1. Adsorption Experiments

Adsorption experiments were carried out with a typical batch approach in a 250 mL round flask with a reflux condenser. In each experiment, 0.02 g of the adsorbent was stirred with 100 mL of a solution containing RB (or MB or a mixture of RB and MB) at a specific concentration, and the temperature of the reactor was fixed at 30 or 45°C. After a certain interval, 5 mL of the solution was withdrawn and centrifuged to remove the adsorbent, and the concentration of the remaining solution was determined. The concentration of dyes was determined with the UV-Vis method on UVD-3000 (Labomed, USA) at $λ_{\max} = 554 nm$ for RB and $λ_{\max} = 664 nm$ for MB (Figure 1). The adsorbed capacity ( $q_{t}$ or $q_{e}$ ) and removal efficiency ( $R$ ) of the dye adsorbed onto the adsorbent were calculated according to the following equations: $\begin{matrix} (1) & q_{t} = \frac{(C_{0} - C_{t}) \times V}{m} (mol \cdot g^{- 1}), \\ (2) & q_{e} = \frac{(C_{0} - C_{e}) \times V}{m} (mol \cdot g^{- 1}), \\ (3) & R = \frac{(C_{0} - C_{e})}{C_{0}} \times 100 (%), \end{matrix}$ where $C_{0}$ and $C_{t}$ are the concentrations of the dyes in the solution (mol·L^-1) at time $t = 0$ and $t = t$ , respectively; $C_{e}$ is the concentration of the dyes in the solution (mol·L^-1) at equilibrium; $V$ is the volume of the solution (L); and $m$ is the weight of the dry adsorbent (g).

Figure 1

UV-Vis absorption spectra for aqueous solutions of (a) RB, (b) MB, and (c) both of the dyes along with alkali-activated diatomite at various adsorption times.

(b)

(c)

The influence of initial pH (3, 5, 7, 9, and 11) was also studied in a single system with a similar procedure.

2.5.2. Isothermal Models

In this work, the Langmuir and Freundlich two-parameter models were used to analyze the adsorption equilibrium data.

The Langmuir model is based on the assumption that the adsorption is a monolayer; that is, the adsorbates form a monolayer and all the sorption sites on the adsorbent surface have the same affinity for the adsorbates. The Langmuir isotherm equation [48] is as follows: $\begin{matrix} (4) & q_{e} = q_{m} \times \frac{K_{L} \times C_{e}}{1 + K_{L} \times C_{e}}, \end{matrix}$ where $q_{m}$ is the maximum monolayer adsorption capacity of the adsorbent (mol·g^-1) and $K_{L}$ is the Langmuir constant (L·mol^-1). The other parameters are described above. The Langmuir constant is a measure of the affinity between the adsorbate and the adsorbent and relates to the free energy of adsorption [5]. The most commonly used linear form of the Langmuir equation [2–5, 13, 18, 20, 32, 42, 49–51] is $\begin{matrix} (5) & \frac{C_{e}}{q_{e}} = \frac{1}{q_{m}} \times C_{e} + \frac{1}{K_{L} \times q_{m}} . \end{matrix}$

The plot of $C_{e} / q_{e}$ versus $C_{e}$ is a straight line with the slope $1 / q_{m}$ and intercept $1 / (q_{m} \cdot K_{L})$ .

The Freundlich expression is an exponential equation and therefore assumes that as the adsorbate concentration increases, the concentration of the adsorbate on the adsorbent surface also increases. The Freundlich isotherm is expressed by the following empirical equation [48]: $\begin{matrix} (6) & q_{e} = K_{F} \times C_{e}^{1 / n}, \end{matrix}$ where $n$ is the heterogeneity factor, and $K_{F}$ is the Freundlich constant (mol^(1-1/n)·L^1/n·g^-1). $n$ and $K_{F}$ are dependent on temperature; $n$ indicates the extent of the adsorption, and $K_{F}$ expresses the degree of nonlinearity between the solution concentration and the adsorption.

The linear form of the Freundlich equation is $\begin{matrix} (7) & \log (q_{e}) = \log (K_{F}) + \frac{1}{n} \times \log (C_{e}) . \end{matrix}$

The plot of $\log (q_{e})$ versus $\log (C_{e})$ is a straight line with the slope $1 / n$ and intercept $\log (K_{F})$ .

2.5.3. Thermodynamic Parameters

To determine whether the adsorption process occurs spontaneously or not, we have to study the thermodynamic parameters. At equilibrium, the Gibbs free energy of adsorption ( $Δ G^{°}$ ) is an important quantity for determining the spontaneity of the process itself and is calculated according to the following equation: $\begin{matrix} (8) & Δ G^{°} = - R \times T \times \ln K_{e}, \end{matrix}$ where $K_{e}$ is the thermodynamic equilibrium constant; $R$ is the universal gas constant (8.314 J·mol^-1·K^-1); and $T$ is the absolute temperature in Kelvin.

For the adsorption process, $K_{e}$ can be determined in a number of ways, depending on the experimental conditions, such as the equilibrium constant $K_{C} = (C_{0} - C_{e}) / C_{e}$ [3, 16, 18, 20, 38], the distribution coefficient $K_{d} = q_{e} / C_{e}$ [12–14, 34, 37, 42, 50–52], and the Langmuir constant $K_{L}$ [4–6, 53, 54].

In this study, the adsorption constant in the Langmuir isotherm ( $K_{L}$ ) was used to determine thermodynamic parameters ( $Δ G^{°}$ , $Δ H^{°}$ , and $Δ S^{°}$ ) for the adsorption by using the following equations [5]: $\begin{matrix} (9) & Δ G^{°} = - R \times T \times \ln K_{L}, \\ (10) & Δ H^{°} = - R \times (\frac{T_{2} \times T_{1}}{T_{2} - T_{1}}) \times \ln \frac{K_{L 1}}{K_{L 2}}, \\ (11) & Δ S^{°} = \frac{Δ H^{°} - Δ G^{°}}{T}, \end{matrix}$ where $K_{L 1}$ and $K_{L 2}$ are adsorption Langmuir constants at $T_{1}$ and $T_{2}$ , $Δ H^{°}$ is the enthalpy change, and $Δ S^{°}$ is the entropy change in a given process.

3. Results and Discussion

3.1. Characterization of Purified and Alkali-Activated Diatomite Samples

As can be seen from Table 2, both the purified and alkali-activated diatomite samples mainly consist of O, Si, Al, and Fe. Alkali-activated diatomite has a lower O and Si content than purified diatomite, and this is probably due to the removal of organic constituents and the dissolution of SiO₂ during alkali treatment. This decrease entrains the increase in the content of Fe and Al.

Table 2

Elemental composition of the diatomite samples ( $w %$ , EDX).

Element	Purified diatomite	Alkali-activated diatomite
O	$52.72 \pm 1.48$	$49.06 \pm 1.27$
Mg	$0.53 \pm 0.06$	$0.53 \pm 0.04$
Al	$10.36 \pm 0.87$	$11.59 \pm 0.03$
Si	$30.56 \pm 0.59$	$27.50 \pm 1.42$
K	$0.20 \pm 0.09$	$1.09 \pm 0.83$
Ca	$0.21 \pm 0.05$	$0.17 \pm 0.03$
Ti	$0.91 \pm 0.17$	$1.23 \pm 0.10$
Fe	$4.50 \pm 0.10$	$6.02 \pm 0.27$
Na	—	$1.77 \pm 0.24$
Cl	—	$1.03 \pm 0.19$
Total	100	100

Both the purified and alkali-activated diatomite samples have an amorphous structure (Figure 2(a)). The broad peaks at 20-25° are typical for amorphous SiO₂ [1, 32, 37, 39, 51]. The absence of the peak around 27° indicates that the diatomite in our study does not contain quartz crystals like other types of diatomite [1, 26, 30, 32, 35, 37, 39, 40].

Figure 2

XRD pattern (a) and FT-IR spectra (b) of the diatomite samples.

(b)

The FT-IR spectra of the diatomite samples are similar (Figure 2(b)). The broad absorption bands at 3450 cm^-1 and 1641 cm^-1 correspond to the adsorbed H₂O, including interlayer water and hydrogen-bonded water with surface hydroxyl groups. A broad band centered at 1101-1031 cm^-1 and two bands at 789 cm^-1 and 465 cm^-1 correspond to the asymmetric stretching vibration, symmetric stretching, and bending vibration of Si-O-Si bonds, respectively [1, 20]. The peaks observed at 3699 cm^-1 and 3623 cm^-1 are assigned to surface hydroxyl groups in diatomite. The peak at 3699 cm^-1 is attributed to the isolated hydroxyl (Si-OH) on the surface of diatomite [1, 43, 55], while the peak at 3623 cm^-1 belongs to O-H stretching vibration of the aluminol groups (≡AlOH) [55]. Alkali-activated diatomite has high-intensity peaks for O–H stretching, indicating that more isolated hydroxyl groups are present on the surface. The peak at 536 cm^-1 corresponds to the stretching vibration of Fe-O [1]. The peak at 1380 cm^-1 is attributed to some organic substances [20]. The intensity of this peak is lower in alkali-activated diatomite than in purified diatomite samples, indicating the removal of organic substances from purified diatomite during NaOH treatment.

The SEM images show that purified diatomite consists of circular cylinders of a diameter of about 5-7 μm, with small pores on the surface (Figures 3(a) and 3(b)). However, these cylinders are partly shattered, causing the pores to become smaller and even blocked. The alkali-activated diatomite retains its multipore structure, and the pores on the surface become larger after treatment (Figures 3(c) and 3(d)). This change may be the result of the formation of soluble silicates ${SiO}_{3}^{2 -}$ from SiO₂ [4]. Another reason for this change is probably the removal of organic constituents, leading to the increase in the pore size and hence the increase of the surface area of alkali-activated diatomite.

Figure 3

SEM images. (a, b) Purified diatomite. (c, d) Alkali-activated diatomite.

(b)

(c)

(d)

Figure 4 shows the nitrogen adsorption-desorption isotherms and pore size distribution of the diatomite samples. The diatomite exhibits a type II isotherm and an H3-type hysteresis loop, indicating the presence of macroporous structures with nonuniform size and/or shape [56]. Thus, the morphology of the diatomite consists of a variety of shapes (Figure 3). However, the pore size distribution curves of the diatomite samples demonstrate a uniform pore size with an average diameter of 4.3 nm. The textural properties of the samples are presented in Table 3. According to the Brunauer-Emmett-Teller analysis, the purified diatomite exhibits a large specific surface area of 55.4 m²/g. This value is consistent with that reported by Son et al. [6] (51 m²/g) for Phu Yen’s diatomite and is much higher than that published in previous works [4, 8, 11, 20, 24, 26, 32, 38, 55] (1.0-27 m²/g). It can be seen from Table 3 that the specific surface area of alkali-activated diatomite (77.8 m²/g) is significantly larger than that of purified diatomite. This increase in the surface area results from the removal of organic impurities during the alkali treatment.

Figure 4

Nitrogen adsorption-desorption isotherms (a) and pore size distributions (b) of the diatomite samples.

(b)

Table 3

Textural properties of the diatomite samples.

Sample	$S_{BET}$ (m²·g^-1)	$S_{mic}$ (m²·g^-1)	$S_{ext}$ (m²·g^-1)	$V_{mic}$ (cm³·g^-1)	$V_{tot}$ (cm³·g^-1)
Purified diatomite	55.4	19.2	36.2	0.0088	0.0623
Alkali-activated diatomite	77.8	19.7	59.1	0.0089	0.0924

The zero charge point of purified diatomite is 5.7 (Figure 5). This pH_PZC is similar to that published in the literature [6, 11, 21, 22]. However, the pH_PZC of alkali-activated diatomite (8.9) is much greater than that of purified diatomite. This increase is probably due to the formation of isolated hydroxyl groups on the surface of the material during alkali treatment.

Figure 5

Determination of the point of zero charge of the diatomite samples.

3.2. Isothermal Studies

3.2.1. Adsorption in Single Systems

(1) Adsorption of RB onto Purified and Alkali-Activated Diatomite Samples. Figures 6 and 7 present the Freundlich and Langmuir isothermal models for the adsorption of RB dye onto the diatomite samples at 30 and 45°C. The isothermal parameters obtained from the experimental data and the respective correlation coefficients are listed in Table 4. It can be seen that the experimental points fit the models well with high correlation coefficients (0.9104-0.9955). Table 4 also shows that the maximal RB adsorption capacity of the alkali-activated diatomite sample is greater than that of the purified diatomite sample. Thus, the activation of diatomite with sodium hydroxide enhances the adsorption of the RB basic dye on diatomite. This enhancement can be attributed to a larger number of the silanol groups formed on the surface, as well as the larger specific surface area of the material.

Figure 6

Freundlich isothermal model for RB adsorption onto diatomite: (a) 30°C and (b) 45°C.

(b)

Figure 7

Langmuir isothermal model for RB adsorption onto diatomite: (a) 30°C and (b) 45°C.

(b)

Table 4

Isotherm parameters for adsorption of RB onto the diatomite.

Sample	Temperature (°C)	Freundlich			Langmuir
Sample	Temperature (°C)	$n$	$K_{F}$	$R^{2}$	$q_{\max}$ (mol·g^–1)	$K_{L}$	$R^{2}$
Purified diatomite	30	2.80	$8.02 \times 10^{- 3}$	0.9738	$2.20 \times 10^{- 4}$	$2.45 \times 10^{5}$	0.9880
Purified diatomite	45	2.97	$6.05 \times 10^{- 3}$	0.9104	$1.93 \times 10^{- 4}$	$3.49 \times 10^{5}$	0.9955
Alkali-activated diatomite	30	2.09	$38.98 \times 10^{- 3}$	0.9833	$3.00 \times 10^{- 4}$	$1.53 \times 10^{5}$	0.9857
Alkali-activated diatomite	45	1.98	$47.23 \times 10^{- 3}$	0.9874	$2.97 \times 10^{- 4}$	$1.23 \times 10^{5}$	0.9856

The results presented above show that alkali-activated diatomite is superior to purified diatomite in terms of chemical and physical properties and adsorption capacity. Therefore, in the following sections, only an alkali-activated diatomite sample is used for the adsorption of dyes from aqueous solutions.

(2) Adsorption of MB onto Alkali-Activated Diatomite. The MB adsorption isotherms onto alkali-activated diatomite were also investigated and analyzed according to the linear Freundlich and Langmuir equations. Analysis results are shown in Figure 8 and Table 5. In this case, the Langmuir model is significantly more suitable to describe the adsorption data than the Freundlich model ( $R^{2} = 0.9874$ -0.9915 as opposed to $R^{2} = 0.7353$ -0.8676). That is, the adsorption mainly occurs in a monolayer. The maximum adsorption capacity of MB on alkali-activated diatomite is $7.14 \times 10^{- 4}$ and $6.90 \times 10^{- 4}$ (mol·g^–1) at 30 and 45°C, respectively.

Figure 8

Plots of the isothermal equations in the linear form for MB adsorption onto alkali-activated diatomite at different temperatures in the single systems: (a) Freundlich and (b) Langmuir.

(b)

Table 5

Isotherm parameters for adsorption of MB onto alkali-activated diatomite in the single systems.

Temperature (°C)	Freundlich			Langmuir
Temperature (°C)	$n$	$K_{F}$	$R^{2}$	$q_{\max}$ (mol·g^–1)	$K_{L}$	$R^{2}$
30	6.59	$2.64 \times 10^{- 3}$	0.8676	$7.14 \times 10^{- 4}$	$1.69 \times 10^{5}$	0.9874
45	6.34	$2.72 \times 10^{- 3}$	0.7353	$6.90 \times 10^{- 4}$	$1.77 \times 10^{5}$	0.9915

3.2.2. Adsorption onto Alkali-Activated Diatomite in Binary Systems

Like in the single system, in the binary system, the adsorption of the dyes at 30 or 45°C also follows the Langmuir isothermal model with the $R^{2}$ values approaching 1 (Figures 9 and 10). The isothermal data in Table 6 also show that the maximum adsorption capacity of alkali-activated diatomite for MB is higher than that for RB, which is similar to the single systems (Tables 4 and 5). Specifically, the ratio of the maximum adsorption capacity of the dyes in the binary system ( $MB / RB = 4.55 \times 10^{- 4} / 1.40 \times 10^{- 4} \approx 3.3$ times at 30°C, and $MB / RB = 4.55 \times 10^{- 4} / 1.40 \times 10^{- 4} \approx 3.1$ times at 45°C) is higher than that in the single system ( $MB / RB = 7.14 \times 10^{- 4} / 3.00 \times 10^{- 4} \approx 2.4$ times at 30°C, and $MB / RB = 6.90 \times 10^{- 4} / 2.97 \times 10^{- 4} \approx 2.3$ times at 45°C). This proves that there is competitive adsorption in the binary system, where MB molecules preferentially adsorb onto alkali-activated diatomite compared with RB molecules. This enhanced adsorption might result from the smaller size of the MB molecule. MB molecules more easily diffuse into the pores of diatomite than RB molecules, thus occupying the adsorption sites on the adsorbent surface before the RB molecules do. Similar results are also reported by Eftekhari et al. [5].

Figure 9

Plots of the isothermal equations in the linear form for the adsorption onto alkali-activated diatomite in the binary systems at 30°C: (a) Freundlich and (b) Langmuir.

(b)

Figure 10

Plots of the isothermal equations in the linear form for the adsorption onto alkali-activated diatomite in the binary systems at 45°C: (a) Freundlich and (b) Langmuir.

(b)

Table 6

Isotherm parameters for the adsorption onto alkali-activated diatomite in the binary systems at different temperatures.

Dye	Temperature (°C)	Freundlich			Langmuir
Dye	Temperature (°C)	$n$	$K_{F}$	$R^{2}$	$q_{\max}$ (mol·g^–1)	$K_{L}$	$R^{2}$
RB	30	14.68	$0.25 \times 10^{- 3}$	0.5081	$1.40 \times 10^{- 4}$	$2.27 \times 10^{5}$	0.9983
RB	45	3.53	$1.88 \times 10^{- 3}$	0.8578	$1.80 \times 10^{- 4}$	$0.37 \times 10^{5}$	0.9905
MB	30	13.00	$0.93 \times 10^{- 3}$	0.6898	$4.55 \times 10^{- 4}$	$5.78 \times 10^{5}$	0.9949
MB	45	7.29	$2.06 \times 10^{- 3}$	0.9288	$5.59 \times 10^{- 4}$	$4.36 \times 10^{5}$	0.9950

Table 7 compares the adsorption capacity of the diatomite samples for RB and MB in this study and that of other adsorbents published in the literature. It can be seen that alkali-activated diatomite has a much higher adsorption capacity than all other adsorbents. Therefore, alkali-activated diatomite might serve as a promising adsorbent for the removal of dyes from aqueous solutions.

Table 7

Maximum adsorption capacity of RB and MB of different adsorbents.

Adsorbent	Adsorption capacity (mg·g^-1)		References
Adsorbent	RB	MB	References
Alkali-activated diatomite	143.9-142.1 $^{}$ 67.0-86.1 $^{ *}$	228.4-220.7 $^{}$ 145.6-178.9 $^{ *}$	The present work
Purified diatomite	105.1-92.2 $^{*}$	—	The present work
Diatomite was treated with H₂SO₄ (1 molar)	—	127	[37]
Purified diatomite	—	72	[37]
Diatomite was treated with sulfuric acid	—	126.6 (30°C)	[3]
Diatomite was treated with sodium hydroxide	—	27.86 (25°C)	[4]
Sodium alginate/silicone dioxide		148.23	[49]
Tagaran natural clay		131.8 (20°C)	[16]
Zeolite 4A		44.35	[19]
AlMCM-41	41.9 (25°C) $^{*}$	66.5 (25°C) $^{*}$	[5]
α-Ag₂WO₄/SBA-15	150	—	[50]
Co and N comodified mesoporous carbon composites	141 (25°C)	—	[57]
Modified banyan aerial roots	115.23	—	[12]
Biosorbent prepared from inactivated Aspergillus oryzae cells	98.59 (293 K)	—	[52]
L-Asp capped Fe₃O₄ NPs	10.44	—	[19]
Silica extracted from rice husk	6.0-6.87	—	[18]

$^{*}$ In single systems and $^{* *}$ in binary systems at 30 and 45°C.

3.3. Thermodynamic Studies

The spontaneity of the adsorption process and the interactions on the liquid/solid interface can be explained by using thermodynamic parameters ( $Δ G^{°}$ , $Δ H^{°}$ , and $Δ S^{°}$ ). If $Δ G^{°} < 0$ , the adsorption process is spontaneous; otherwise, adsorption does not occur on its own. If $Δ H^{°} < 0$ , the adsorption process is exothermic and vice versa. If $Δ S^{°} > 0$ , it is possible to infer that the adsorbent affinity for the dye increases, leading to the increase in randomness of the adsorbates at the liquid/solid interface [4, 42]; in contrast, if $Δ S^{°} < 0$ , more adsorbate molecules adhere to the adsorbent surface [13, 16, 37].

The thermodynamic parameters of RB and MB adsorption onto the diatomite samples are calculated from Equations (9)–(11). The $Δ G^{°}$ of adsorption is negative for both the single and binary systems (Tables 8 and 9), indicating the spontaneity of adsorption processes. The values of $Δ H^{°}$ and $Δ S^{°}$ differ between the adsorption processes, indicating that the adsorption process is complex. Both the physical and chemical adsorption mechanisms are possible.

Table 8

Thermodynamic parameters for adsorption of RB onto purified diatomite in single systems.

Temperature (°C)	$Δ G^{°}$ (kJ·mol^-1)	$Δ H^{°}$ (kJ·mol^-1)	$Δ S^{°}$ (J·mol^-1·K^-1)
30	-31.26	18.90	165.53
45	-33.74

Table 9

Thermodynamic parameters for the adsorption of the dyes onto alkali-activated diatomite.

Dye	Temperature (°C)	Single system			Binary system
Dye	Temperature (°C)	$Δ G^{°}$ (kJ·mol^-1)	$Δ H^{°}$ (kJ·mol^-1)	$Δ S^{°}$ (J·mol^-1·K^-1)	$Δ G^{°}$ (kJ·mol^-1)	$Δ H^{°}$ (kJ·mol^-1)	$Δ S^{°}$ (J·mol^-1·K^-1)
RB	30	-30.08	-11.96	59.79	-31.07	-96.42	-215.69
RB	45	-30.98			-27.83
MB	30	-30.32	2.48	108.27	-33.42	-15.04	60.66
MB	45	-31.94			-34.33

3.4. Effect of Solution pH

Figure 11 shows the effect of solution pH on the adsorption of RB and MB onto alkali-activated diatomite in the single system. The pH of the solution was adjusted between 3 and 11 with a 0.1 M HCl or 0.1 M NaOH solution.

Figure 11

Removal efficiency of the dye onto alkali-activated diatomite at different initial solution pHs in the single systems: (a) RB and (b) MB (adsorbent dosage 0.2 g·L^-1, initial RB concentration $2.09 \times 10^{- 5} mol \cdot L^{- 1}$ , initial MB concentration $3.13 \times 10^{- 5} mol \cdot L^{- 1}$ , and 30°C).

(b)

As can be seen from Figure 11(a), the adsorption efficiency of RB reaches 94% after 240 min of contact at pH 3. At higher pH, this efficiency decreases drastically, reaching 37% up to pH 5–9 and even lower (30%) at pH 11. We know that RB has a carboxylic group in its molecule, and this group dissociates at higher pHs of the solution. This dissociation renders the molecule negative, resulting in the electric repulsion between RB and the negative surface of the adsorbent at high pH. This result is consistent with that of Eftekhari et al. [5].

For MB (Figure 11(b)), the adsorption efficiency reaches 100% after a short time (60 min) of contact at pH 3–9. The efficiency only decreases to around 60% at pH 11.

The zero charge point of alkali-activated diatomite is 8.9 (Figure 5). Theoretically, the surface of the material is positively charged when $pH < 8.9$ and negatively charged when $pH > 8.9$ . This means that when the pH of the dye solution increases, the adsorption efficiency should increase because the negatively charged diatomite surface attracts the dye cations. However, in both of our cases, the adsorption efficiency decreases with pH, especially at pH 11. This demonstrates that the adsorption process is complex, and the electrostatic interaction mechanism is not suitable to describe the adsorption of RB and MB onto alkali-activated diatomite.

4. Conclusions

Alkali-activated diatomite is applied to adsorb RB and MB in the single and binary systems. The treatment with sodium hydroxide increases the surface area of the diatomite from 55.4 m²/g to 77.8 m²/g and creates a large number of free silanol groups on the surface of the material. This increases the material’s ability to adsorb RB and MB. The adsorption equilibrium data of RB and MB onto alkali-activated diatomite fit the Langmuir model in both the single and binary systems. MB has a higher affinity to the adsorbent than RB, and the binary system is more effective than the single system. The adsorption process is spontaneous, and the removal efficiency of both MB and RB depends on pH significantly.

Footnotes

Data Availability

The data used to support the findings of this study are available from the corresponding author upon request.

Conflicts of Interest

The authors declare that they have no conflicts of interest.

Acknowledgments

This research is funded by Thu Dau Mot University under grant number DT.21.1-018.

References

Dai

Liang

Potgieter

Mn-doped Fe₂O₃/diatomite granular composite as an efficient Fenton catalyst for rapid degradation of an organic dye in solution

Journal of Sol-Gel Science and Technology 2021 97

1014354

2 329 339

10.1007/s10971-020-05452-3

Allen

S. J.

Mckay

Porter

J. F.

Adsorption isotherm models for basic dye adsorption by peat in single and binary component systems

Journal of Colloid and Interface Science 2004 280

1014354

2 322 333

10.1016/j.jcis.2004.08.078

2-s2.0-7944239074

15533404

al-Qodah

Lafi

W. K.

al-Anber

al-Shannag

Harahsheh

Adsorption of methylene blue by acid and heat treated diatomaceous silica

Desalination 2007 217

1014354

1-3 212 224

10.1016/j.desal.2007.03.003

2-s2.0-35748958424

Zhang

Ping

Niu

Shi

Kinetics and equilibrium studies from the methylene blue adsorption on diatomite treated with sodium hydroxide

Applied Clay Science 2013 83-84

1014354

12 16

10.1016/j.clay.2013.08.008

2-s2.0-84883537013

Eftekhari

Habibi-Yangjeh

Sohrabnezhad

Application of AlMCM-41 for competitive adsorption of methylene blue and rhodamine B: thermodynamic and kinetic studies

Journal of Hazardous Materials 2010 178

1014354

1-3 349 355

10.1016/j.jhazmat.2010.01.086

2-s2.0-77951498775

20167425

Dang Son

B. H.

Quang Mai

Xuan du

Hai Phong

Quang Khieu

A study on Astrazon Black AFDL dye adsorption onto Vietnamese diatomite

Journal of Chemistry 2016 2016

1014354

8685437

10.1155/2016/8685437

2-s2.0-84978640765

Son

B. H. D.

Mai

V. Q.

D. X.

Phong

N. H.

Cuong

N. D.

Khieu

D. Q.

Catalytic wet peroxide oxidation of phenol solution over Fe-Mn binary oxides diatomite composite

Journal of Porous Materials 2017 24

1014354

3 601 611

10.1007/s10934-016-0296-7

2-s2.0-84990841463

Padmanabhan

S. K.

Pal

Licciulli

Diatomite/silver phosphate composite for efficient degradation of organic dyes under solar radiation

Bulletin of Materials Science 2020 43

1014354

1 295

10.1007/s12034-020-02269-2

Zhang

Y. L.

Yang

X. J.

Preparation, characterization, and adsorption-photocatalytic activity of nano TiO₂ embedded in diatomite synthesis materials

Rare Metals 2017 36

1014354

12 987 991

10.1007/s12598-014-0290-7

2-s2.0-84901887336

10.

Aivalioti

Vamvasakis

Gidarakos

BTEX and MTBE adsorption onto raw and thermally modified diatomite

Journal of Hazardous Materials 2010 178

1014354

1-3 136 143

10.1016/j.jhazmat.2010.01.053

2-s2.0-77951087665

20133057

11.

Chang

Zhang

Tan

Wang

Liu

Xue

New insight into the removal of Cd(II) from aqueous solution by diatomite

Environmental Science and Pollution Research 2020 27

1014354

9 9882 9890

10.1007/s11356-020-07620-y

31927734

12.

Fan

Wan

Wang

Removal of gentian violet and rhodamine B using banyan aerial roots after modification and mechanism studies of differential adsorption behaviors

Environmental Science and Pollution Research 2020 27

1014354

9 9152 9166

10.1007/s11356-019-07024-7

31916156

13.

Paredes-Quevedo

L. C.

González-Caicedo

Torres-Luna

J. A.

Carriazo

J. G.

Removal of a textile azo-dye (basic red 46) in water by efficient adsorption on a natural clay

Water Air & Soil Pollution 2021 232

1014354

1 4

10.1007/s11270-020-04968-2

14.

Z. H.

Zhai

S. R.

Guo

T. M.

Song

Zhang

H. C.

Removal of methylene blue over low-cost mesoporous silica nanoparticles prepared with naturally occurring diatomite

Journal of Sol-Gel Science and Technology 2018 88

1014354

3 541 550

10.1007/s10971-018-4859-8

2-s2.0-85055693934

15.

Vimonses

Lei

Jin

Chow

C. W. K.

Saint

Kinetic study and equilibrium isotherm analysis of Congo Red adsorption by clay materials

Chemical Engineering Journal 2009 148

1014354

2-3 354 364

10.1016/j.cej.2008.09.009

2-s2.0-61649086921

16.

Aziz

B. K.

Shwan

D. M. S.

Kaufhold

Comparative study on the adsorption efficiency of two different local clays for the cationic dye; application for adsorption of methylene blue from medical laboratories wastewater

Silicon 2021

10.1007/s12633-020-00833-3

17.

Singh

Kumar

Gupta

Activated banana peel carbon: a potential adsorbent for rhodamine B decontamination from aqueous system

Applied Water Science 2020 10

1014354

8 185

10.1007/s13201-020-01274-4

18.

Tsamo

Kidwang

G. D.

Dahaina

D. C.

Removal of rhodamine B from aqueous solution using silica extracted from rice husk

SN Applied Science 2020 2

1014354

2 256

10.1007/s42452-020-2057-0

19.

Belachew

Tadesse

Kahsay

M. H.

Meshesha

D. S.

Basavaiah

Synthesis of amino acid functionalized Fe₃O₄ nanoparticles for adsorptive removal of rhodamine B

Applied Water Science 2021 11

1014354

2 33

10.1007/s13201-021-01371-y

20.

Liu

Zhang

Sheng

Ping

Adsorption and release kinetics, equilibrium, and thermodynamic studies of hymexazol onto diatomite

ACS Omega 2020 5

1014354

45 29504 29512

10.1021/acsomega.0c04449

33225181

21.

al-Ghouti

M. A.

Khraisheh

M. A. M.

Allen

S. J.

Ahmad

M. N.

The removal of dyes from textile wastewater: a study of the physical characteristics and adsorption mechanisms of diatomaceous earth

Journal of Environmental Management 2003 69

1014354

3 229 238

10.1016/j.jenvman.2003.09.005

2-s2.0-0348077490

14580724

22.

al-Ghouti

M. A.

Khraisheh

M. A. M.

Ahmad

M. N. M.

Allen

Adsorption behaviour of methylene blue onto Jordanian diatomite: a kinetic study

Journal of Hazardous Materials 2009 165

1014354

1-3 589 598

10.1016/j.jhazmat.2008.10.018

2-s2.0-64549089961

19022576

23.

Piri

Sepehr

Samadi

Farhadi

K. H.

Alizadeh

Contaminated soil amendment by diatomite: chemical fractions of zinc, lead, copper and cadmium

International Journal of Environmental Science and Technology 2020 18

1014354

5 1191 1200

10.1007/s13762-020-02872-0

24.

Nguyen

M. B.

Nguyen

T. V.

G. H.

Pham

T. T. T.

le van

Pham

G. T. T.

Nguyen

T. N.

Tran

Q. V.

T. A.

High CO Adsorption Performance of CuCl-Modified Diatomites by Using the Novel Method “Atomic Implantation”

Journal of Chemistry 2021 2021

1014354

9762578

10.1155/2021/9762578

25.

Sun

Wang

Constructing nanostructured silicates on diatomite for Pb(II) and Cd(II) removal

Journal of Materials Science 2019 54

1014354

9 6882 6894

10.1007/s10853-019-03388-w

2-s2.0-85060946992

26.

Ren

Zhu

Zhang

Zeng

Selective adsorption of PHC and regeneration of washing effluents by modified diatomite

Water Science & Technology 2020 81

1014354

10 2066 2077

10.2166/wst.2020.262

32701487

27.

al-Ghouti

M. A.

al-Degs

Y. S.

Khraisheh

M. A. M.

Ahmad

M. N.

Allen

S. J.

Mechanisms and chemistry of dye adsorption on manganese oxides-modified diatomite

Journal of Environmental Management 2009 90

1014354

11 3520 3527

10.1016/j.jenvman.2009.06.004

2-s2.0-69349085680

19570604

28.

Bahramian

Ardejani

F. D.

Mirkhani

Badii

Diatomite-supported manganese Schiff base: an efficient catalyst for oxidation of hydrocarbons

Applied Catalysis A: General 2008 345

1014354

1 97 103

10.1016/j.apcata.2008.04.028

2-s2.0-45849141554

29.

Quang Khieu

Dang Son

B. H.

Thi Thanh Chau

Dinh du

Hai Phong

Thi Diem Chau

3-Mercaptopropyltrimethoxysilane modified diatomite: preparation and application for voltammetric determination of lead (II) and cadmium (II)

Journal of Chemistry 2017 2017

1014354

9560293

10.1155/2017/9560293

2-s2.0-85016510917

30.

Ren

Qin

Uniform surface modification of diatomaceous earth with amorphous manganese oxide and its adsorption characteristics for lead ions

Applied Surface Science 2014 317

1014354

724 729

10.1016/j.apsusc.2014.08.184

2-s2.0-84908208898

31.

Dong

Q. Y.

Fang

Y. C.

Tan

Ontiveros-Valencia

Zhao

H. P.

Antimonate removal by diatomite modified with Fe-Mn oxides: application and mechanism study

Environmental Science and Pollution Research 2020 28

1014354

11 13873 13885

10.1007/s11356-020-11592-4

33201506

32.

Huang

Chen

Preparation of new diatomite-chitosan composite materials and their adsorption properties and mechanism of Hg(II)

Royal Society Open Science 2017 4

1014354

12 170829

10.1098/rsos.170829

2-s2.0-85038584263

29308226

33.

Ediz

Bentli

İ.

Tatar

İ.

Improvement in filtration characteristics of diatomite by calcination

International Journal of Mineral Processing 2010 94

1014354

3-4 129 134

10.1016/j.minpro.2010.02.004

2-s2.0-77950339094

34.

Yang

Zhang

Wang

Cao

Hursthouse

Preparation of a thermally modified diatomite and a removal mechanism for 1-naphthol from solution

Water 2017 9

1014354

9 651

10.3390/w9090651

2-s2.0-85028807216

35.

Şan

Gören

Özgür

Purification of diatomite powder by acid leaching for use in fabrication of porous ceramics

International Journal of Mineral Processing 2009 93

1014354

1 6 10

10.1016/j.minpro.2009.04.007

2-s2.0-68149167117

36.

Zhang

Cai

Wang

Zhang

Microstructural modification of diatomite by acid treatment, high-speed shear, and ultrasound

Microporous and Mesoporous Materials 2013 165

1014354

106 112

10.1016/j.micromeso.2012.08.005

2-s2.0-84865780237

37.

Ebrahimi

Kumar

Diatomite chemical activation for effective adsorption of methylene blue dye from model textile wastewater

International Journal of Environmental Science and Development 2021 12

1014354

1 23 28

10.18178/ijesd.2021.12.1.1313

38.

Zhao

Y. H.

Geng

J. T.

Cai

J. C.

Cai

Y. F.

Cao

C. Y.

Adsorption performance of basic fuchsin on alkali-activated diatomite

Adsorption Science & Technology 2020 38

1014354

5-6 151 167

10.1177/0263617420922084

39.

Jin

Ouyang

Yang

One-step synthesis of highly ordered Pt/MCM-41 from natural diatomite and the superior capacity in hydrogen storage

Applied Clay Science 2014 99

1014354

246 253

10.1016/j.clay.2014.07.001

2-s2.0-84906943206

40.

Servatan

Ghadiri

Yazdi

M. K.

Jouyandeh

Mahmodi

Samadi

Zarrintaj

Habibzadeh

Ganjali

M. R.

Saeb

M. R.

Synthesis of cost-effective hierarchical MFI-type mesoporous zeolite: introducing diatomite as silica source

Silicon 2020

10.1007/s12633-020-00786-7

41.

Simonenko

E. P.

Simonenko

N. P.

Zharkov

M. A.

Shembel

N. L.

Simonov-Emel’yanov

I. D.

Sevastyanov

V. G.

Kuznetsov

N. T.

Preparation of high-porous SiC ceramics from polymeric composites based on diatomite powder

Journal of Materials Science 2015 50

1014354

2 733 744

10.1007/s10853-014-8633-1

2-s2.0-84911987908

42.

Zhang

Cui

Zhang

Meng

Synthesis of zeolite Y from diatomite and its modification by dimethylglyoxime for the removal of Ni(II) from aqueous solution

Journal of Sol-Gel Science and Technology 2016 80

1014354

1 215 225

10.1007/s10971-016-4080-6

2-s2.0-84970004230

43.

Yuan

D. Q.

H. P.

Lin

Z. Y.

The hydroxyl species and acid sites on diatomite surface: a combined IR and Raman study

Applied Surface Science 2004 227

1014354

1-4 30 39

10.1016/j.apsusc.2003.10.031

2-s2.0-1842477700

44.

Shyam

Puri

J. K.

Kaur

Amutha

Kapila

Single and binary adsorption of heavy metals on fly ash samples from aqueous solution

Journal of Molecular Liquids 2013 178

1014354

31 36

10.1016/j.molliq.2012.10.031

2-s2.0-84870835808

45.

Mahmood

Saddique

M. T.

Naeem

Westerhoff

Mustafa

Alum

Comparison of different methods for the point of zero charge determination of NiO

Industrial & Engineering Chemistry Research 2011 50

1014354

17 10017 10023

10.1021/ie200271d

2-s2.0-80052379636

46.

Jing

H. P.

Wang

C. C.

Zhang

Y. W.

Wang

Photocatalytic degradation of methylene blue in ZIF-8

RSC Advances 2014 4

1014354

97 54454 54462

10.1039/C4RA08820D

2-s2.0-84908518070

47.

Dinh du

Ngoc Hoai

Synthesis of MIL-53(Fe) metal-organic framework material and its application as a catalyst for Fenton-type oxidation of organic pollutants

Advances in Materials Science and Engineering 2021 2021

1014354

5540344

10.1155/2021/5540344

48.

Hamdaoui

Naffrechoux

Modeling of adsorption isotherms of phenol and chlorophenols onto granular activated carbon: Part I. Two-parameter models and equations allowing determination of thermodynamic parameters

Journal of Hazardous Materials 2007 147

1014354

1-2 381 394

10.1016/j.jhazmat.2007.01.021

2-s2.0-34447632624

17276594

49.

Hosseinzadeh

Abdi

Efficient removal of methylene blue using a hybrid organic-inorganic hydrogel nanocomposite adsorbent based on sodium alginate-silicone dioxide

Journal of Inorganic and Organometallic Polymers and Materials 2017 27

1014354

6 1595 1612

10.1007/s10904-017-0625-6

2-s2.0-85025146224

50.

Silva

F. C. M.

Silva

L. K. R.

Santos

A. G. D.

Caldeira

V. P. S.

Cruz-Filho

J. F.

Cavalcante

L. S.

Longo

Luz

G. E.

Structural refinement, morphological features, optical properties, and adsorption capacity of α-Ag₂WO₄ nanocrystals/SBA-15 mesoporous on rhodamine B dye

Journal of Inorganic and Organometallic Polymers and Materials 2020 30

1014354

9 3626 3645

10.1007/s10904-020-01560-3

51.

Liu

Chen

Zheng

J. G.

Removal of iodate from aqueous solution using diatomite/nano titanium dioxide composite as adsorbent

Journal of Radioanalytical and Nuclear Chemistry 2020 324

1014354

3 1179 1188

10.1007/s10967-020-07161-1

52.

Souza

F. H. M.

Leme

V. F. C.

Costa

G. O. B.

Castro

K. C.

Giraldi

T. R.

Andrade

G. S. S.

Biosorption of rhodamine B using a low-cost biosorbent prepared from inactivated Aspergillus oryzae cells: kinetic, equilibrium and thermodynamic studies

Water Air & Soil Pollution 2020 231

1014354

5 242

10.1007/s11270-020-04633-8

53.

My Linh

N. L.

Hoang van

Duong

Tinh

M. X.

Quang Khieu

Adsorption of arsenate from aqueous solution onto modified Vietnamese bentonite

Advances in Materials Science and Engineering 2019 2019

1014354

2710926

10.1155/2019/2710926

2-s2.0-85065780126

54.

Thi Huong

Son

N. N.

Phuong

V. H.

Dung

C. T.

Huong

P. T. M.

Son

L. T.

Synthesis Fe₃O₄/talc nanocomposite by coprecipition-ultrasonication method and advances in hexavalent chromium removal from aqueous solution

Adsorption Science & Technology 2020 38

1014354

9-10 483 501

10.1177/0263617420969112

55.

S. C.

Wang

Z. G.

Zhang

J. L.

Sun

D. H.

Liu

G. X.

Detection analysis of surface hydroxyl active sites and simulation calculation of the surface dissociation constants of aqueous diatomite suspensions

Applied Surface Science 2015 327

1014354

453 461

10.1016/j.apsusc.2014.12.006

2-s2.0-84921664545

56.

Leofanti

Padovan

Tozzola

Venturelli

Surface area and pore texture of catalysts

Catalysis Today 1998 41

1014354

1-3 207 219

10.1016/S0920-5861(98)00050-9

2-s2.0-0001195750

57.

Zheng

Liu

Wang

In-situ carbonization of ZIF-67 to fabricate magnetically Co/N-mC with high adsorption capacity toward water remediation

SN Applied Sciences 2021 3

1014354

1 111

10.1007/s42452-021-04186-3

Single and Binary Adsorption Systems of Rhodamine B and Methylene Blue onto Alkali-Activated Vietnamese Diatomite

Abstract

1. Introduction

2. Materials and Methods

2.1. Materials

2.2. Activation of Diatomite

2.3. Characterization

2.4. Point of Zero Charge

2.5. Adsorption

2.5.1. Adsorption Experiments

2.5.2. Isothermal Models

2.5.3. Thermodynamic Parameters

3. Results and Discussion

3.1. Characterization of Purified and Alkali-Activated Diatomite Samples

3.2. Isothermal Studies

3.2.1. Adsorption in Single Systems

3.2.2. Adsorption onto Alkali-Activated Diatomite in Binary Systems

3.3. Thermodynamic Studies

3.4. Effect of Solution pH

4. Conclusions

Footnotes

Data Availability

Conflicts of Interest

Acknowledgments

References