Synthesis of Fe₂O₃/TiO₂/graphene aerogel composite as an efficient Fenton-Photocatalyst for removal of methylene blue from aqueous solution
Cite this paper: Vietnam J. Chem., 2020, 58(5), 697-704
DOI: 10.1002/vjch.202000109
Article
Synthesis of Fe2O3/TiO2/graphene aerogel composite as
an efficient Fenton-photocatalyst for removal of methylene blue
from aqueous solution
Tran Hoang Tu1,3, Le Tan Tai1,3, Nguyen Tan Tien1, Le Minh Huong2,3, Doan Thi Yen Oanh4,
Hoang Minh Nam1,2,3, Mai Thanh Phong2,3, Nguyen Huu Hieu1,2,3*
1VNU-HCM Key Laboratory of Chemical Engineering and Petroleum Processing (CEPP Lab), Ho Chi Minh
City University of Technology, 268 Ly Thuong Kiet Street, district 10, Ho Chi Minh City 70000, Viet Nam
2Faculty of Chemical Engineering, Ho Chi Minh City University of Technology,
268 Ly Thuong Kiet street, district 10, Ho Chi Minh City 70000, Viet Nam
3Vietnam National University Ho Chi Minh City,
6,Linh Trung ward, Thu Duc district, Ho Chi Minh City 70000, Viet Nam
4Publishing House for Science and Technology, Vietnam Academy of Science and Technology,
18 Hoang Quoc Viet, Cau Giay district, Hanoi 10000, Viet Nam
Submitted July 6, 2020; Accepted September 4, 2020
Abstract
In the present study, the composites including Fe2O3/TiO2/graphene aerogel (Fe2O3/TiO2/GA) and TiO2/graphene
aerogel (TiO2/GA), and graphene aerogel (GA) were synthesized by hydrothermal method. The as-prepared materials
were characterized using X-ray diffraction, Fourier transform infrared spectroscopy, scanning electron microscopy,
energy dispersive X-ray, Raman spectroscopy. The characterization results showed that the Fe2O3 and TiO2 particles
were uniformly attached in GA structure, increasing number of active sites of materials and extending the light
absorption range. The removal performance of Fe2O3/TiO2/GA is 97.38 % which is higher than of TiO2/GA and TiO2.
The degradation data were well consisted with pseudo-first-order kinetic model. Accordingly, Fe2O3/TiO2/GA is
potential to be used as an efficient photocatalysis for treatment of MB from water.
Keywords. Fe2O3, TiO2, Graphene aerogel, nanocomposite, photocatalysis, methylene blue.
1. INTRODUCTION
utilized to separate these organic dyes such as
advanced oxidation processes (AOPs),
Recently, water pollution is an increasing global photocatalysis, adsorption, membranes, and
problem. The industrialization in developing biological degradation.[3]
countries has led to a mass discharge of organic dyes AOPs have developed based on the performance
into water. These agents are important source used of highly reactive and nonselective hydroxyl radicals
in various industries comprising
textile, (OH•), which have the oxidizing capability to
pharmaceuticals, food, paper, and cosmetic. The remove non-biodegradable organic compounds in
molecular structure of organic dyes is highly water. Among a variety of AOPs, Fenton process
stability, persistent for a long time, and resistant to based the catalysis effect of Fe3+/Fe2+ with H2O2
biodegradation in aqueous solution.[1] Organic agents to generate the OH• radical, reacting with
matter
can
cause
oxygen
depletion, organic compounds to decompose into CO and H2O.
immunosuppression, reproductive failure and acute However, the Fenton process has a few drawbacks:
poisoning in aquatic organisms. The presence of (i) low utilization efficiency of the generated active
dyes has significant impact on the human health species, (ii) incomplete removal of dye pollutants,
because even the smallest amount of these agents is (iii) applicable at low pH (pH 2-4), (iv) difficult to
toxic or even carcinogenic.[2] Consequently, the
developing effective handling methods are urgently
necessitated. To date, various techniques have been
separate
and
reuse
catalysts.[4,5]
To increase the efficiency of AOPs, the recent
studies have pay attention to the development of
697 Wiley Online Library © 2020 Vietnam Academy of Science and Technology, Hanoi & Wiley-VCH GmbH
Vietnam Journal of Chemistry
Nguyen Huu Hieu et al.
heterogeneous Fenton-like catalysts in removing
organic pollutants from wastewater. Titanium oxide
2.1. Materials
(TiO2) is the most common semiconductor All chemicals including graphite (99 wt.%, 20 µm),
photocatalyst used due to its potential benefits such
as low cost, non-toxicity, and high stablity. The
agglomeration of particles phenomenon and the
recombination of photo generated electron-hole pairs
decreased the degradation efficiency of TiO2.
Additionally, the TiO2 has a large band gap (Eg = 3.2
eV) which absorbed in the ultraviolet light region.
To tackle the mentioned above, TiO2 has been doped
and coupled with various materials such as Fe2O3,
ZnO, WO3, etc. to extent the light absorption and
improve the degradation activity of organic
pollutant.[3]
titanium(IV) isopropoxide (Ti[(OCH(CH₃)2]4, 97
wt.%), ferric nitrate (Fe(NO3)3.9H2O, 99 wt.%),
sulfuric acid (H2SO4, 98 wt.%), hydrochloric acid
(HCl, 36 wt.%), phosphoric acid (H3PO4, 85 wt.%),
and hydrogen peroxide (H2O2, 30 wt.%) were
purchased
from
Sigma-Aldrich,
Germany.
Potassium permanganate (KMnO4, 99 wt.%), MB
(99 %), sodium hydroxide (NaOH, 99 wt.%), and
ethanol (C2H5OH, 99 wt.%) were purchased from
Vina Chemsol, Vietnam. There are no any further
purification to all chemicals that were analysed and
were used as received.
Hematite (α-Fe2O3), is an iron(III) oxide form,
has attracted countless attention due to its diversity
in characteristics including low cost, low toxicity,
high stability, excellent optical properties,
environmental friendly, narrow band gap (2.0-2.2
eV), and oxidative nature.[3] The combination of
TiO2 with Fe2O3 to form the heterostructure was
considered as an effective way to lower the band gap
energy level and improve the absorption light
efficiency of the catalyst. Simultaneously, the
attaching Fe2O3 and TiO2 particles to the substrate to
increase surface area and promote removal
efficiency. Graphene aerogel (GA), is a three-
dimensional (3D) graphene-based structure, contains
many outstanding properties including low density,
high porosity and surface area, low thermal
conductivity, and high electric conductivity. The GA
substrate enabes to create the small size
nanoparticles and elevate the production of free
radical and advancing the catalytic efficiency of
material. Besides, GA substrate promotes the
transfer of electrons to prevent the recombination
rate of electrons-holes.[6,7] In addition, GA has high
adsorption capacity of dye to increase the contact
surface of dye with catalyst, enhancing the irradiated
performance of catalyst.
2.2. Synthesis of GO
Graphene oxide (GO) was fabricated by improved
Hummers’ method from graphite.[8] Initially, 3 g of
graphite was added into 360 mL of H2SO4 and 40
mL H3PO4. After that, 18 g KMnO4 was added
slowly into the mixture, and stirred for 30 minutes in
an ice bath. Then, the mixture was continued to be
o
stirred at 50 C for 12 hours and cooled to room
temperature. The resulting mixture was added with
500 mL of water, 15 mL of H2O2, centrifuged. The
pH of the centrifuged mixture was adjusted to 6 by
using 10 % HCl, water, and ethanol. Graphite oxide,
which is the resulting solid, (GiO) was obtained,
o
dried at 50 C and dispersed in water (1 mg/mL).
Afterward, GO suspension, which was acquired after
12 hours of ultrasonication. The suspension was
centrifuged and dried at 50 C to attain GO as the
o
final product.
2.3. Synthesis of Fe2O3-TiO2/GA
Graphene aerogel (GA) was prepared by self-
assembly process of rGO sheets under hydrothermal
conditions.[9] TiO2/graphene aerogel (TiO2/GA) was
In this work, TiO2/GA and Fe2O3 -TiO2/GA
composite were synthersized by hydrothermal
method. The samples were characterized by powder
prepared
by
hydrothermal
method
with
Ti[(OCH(CH₃)]2:GO mass ratio of 1:1. The Fe2O3-
TiO2/GA nanocomposite was synthesized by
hydrothermal method according to the studies. [3, 10]
In a typical synthetic procedure, 0.12 g of
Fe(NO3)3.9H2O was dissolved into 80 mL of GO
suspension (5 mg/mL) under vigorously stirring.
Then, 280 µL of Ti[(OCH(CH₃)2]4 was added
dropwise into the mixture and sonicated for 2 hours.
Afterward, the mixture was transferred and sealed
into a Teflon-lined autoclave 100 mL, followed by a
(FTIR), scanning
electronic
microscopy (SEM), energy-dispersive X-ray
samples were applied as Fenton photocatalysis to
degrade methylene blue (MB) from water. Besides,
the kinetic and reusability of material for methylene
blue degradation were also evaluated.
o
heating at 180 C for 12 hours. The as-synthesized
2. MATERIALS AND METHODS
hydrogel was immersed in ethanol/water mixture
Vietnam Journal of Chemistry
Synthesis of Fe2O3/TiO2/graphene…
with a ratio of 3:1 for 24 h. Then, the hydrogel was XRD patterns of GA, TiO2/GA, and Fe2O3-TiO2/GA
freeze-dried to obtain TiO2/GA.
are shown in figure 1. GA had a wide peak at
2θ = 24°, corresponding to the diffraction (0 0 2)
peak. Based on the Bragg equation, the interlayer
distance between layers in GA was determined to be
0.37 nm, which lower than of GO (0.82 nm) and
higher than of graphite (0.34 nm). This phenomenon
2.4. Characterization
The synthesized materials were characterized by
XRD (Advanced X8, Bruker, Germany), FTIR
(Alpha-E, Bruker, Germany), Raman spectroscopy was confirmed the partially removal of oxygen-
(LabRAM HR Evolution, Horiba, Japan SEM containing groups in GO structure, owing to the
(Hitachi S-4800, Japan), EDX (Jeol JMS 6490, incomplete of reduction process of GO to rGO.
JEOL, Japan), and UV-visible spectroscopy (UV-
Vis, Horiba Dual FL, Japan).
Besides, the decrease in intensity of (0 0 2) peak
showed to the self-assembly of rGO sheets to form
GA. As for TiO2/GA, the diffraction peaks were
presented at 2 = 25.39, 37.78, 47.97, 53.95, 54.90,
62.64, 68.89, 70.24, and 75.00o assigning to
crystalline planes (1 0 1), (0 0 4), (2 0 0), (1 0 5),
(2 1 1), (2 0 4), (1 1 6), (2 2 0), and (2 1 5) of
anatase TiO2, respectively (JCPDS No. 21-1272).[11]
In Fe2O3-TiO2/GA, the peaks of TiO2 were also
reported. And, the characteristic diffraction peaks of
α-Fe2O3 were detected at 33.21 (1 0 4), 36.12 (1 1
0), 41.75 (1 1 3), 50.08 (024), 53.68 (1 1 6), 57.73
(122), and 65.17° (3 0 0) (JCPDS No. 01-1030).[12]
Thus, the Fe2O3 and TiO2 particles were docked on
the GA structure. By using the Scherrer equation,
the size of particles on Fe2O3-TiO2/GA was fell in
the range of 0.5-3.5 nm as shown in table 1. The
relatively low characteristic peak of TiO2 indicates
that a reduction in size of particles in Fe2O3-
TiO2/GA compared to TiO2/GA, showing the
replacement of Ti4+ by Fe3+ ions.[3]
2.5. Photo-Fenton degradation experiments
The photocatalytic activities of the synthesized
materials were calculated via photocatalytic
degradation in MB aqueous solution. The effect of
conditions on the removal efficiency is investigated
through Batch experiments. A 25W UV lamp
(Natural light PT 2191-ExoTerra) with wavelength
region from 280 to 320 nm as the irradiation source
was placed above the reactor. In a typical, 20 mg of
catalysts and the 20 mL MB solution with initial
concentration of 50 mg/L were mixed together. A
change to 7 occurred in the pH of the mixture. The
mixture was stirred in the dark for 30 min to achieve
adsorption equilibrium. Then, 2 mL of H2O2 was
added in MB solution and the lamp was turned on,
the photo Fenton-like reaction occurred. After the
illumination time, the solution was filtered through
0.45 μm Nylon syringe filter. The residual MB
concentration of solution was measured on UV-Vis
spectrophotometer (Dual FL, Horiba, Japan) at 664
nm. The efficiency of materials for degradation of
MB was calculated from the equation as follow:
Table 1: The average crystallite sizes of particles in
TiO2/GA and Fe2O3-TiO2/GA
Crystallite sizes, nm
Materials
C −C
0
t 100 %
(1)
TiO2
21.20
3.43
Fe2O3
-
0.38
H =
C
0
TiO2/GA
Fe2O3-TiO2/GA
where H (%) is the removal performance of material,
C0 (mg/L) is the initial concentration of MB
solution, and Ct (mg/L) is the concentration of MB
after a certain irradiation time, t.
The kinetics of photocatalytic degradation of MB
in aqueous solution was investigated by the pseudo-
Figure 2 shows the FTIR spectra of GA,
TiO2/GA, and Fe2O3-TiO2/GA. The absorption
bands at around 3550, 1600, and 1250 cm-1
corresponding to the -OH, C=C, and C-O groups
were observed in samples.[2] The bands of oxygen-
containing groups were almost removed, indicating
that GO is reduced and self-assembled to become
GA. Besides, the broad bands below 1000 cm-1 were
allocated to the stretching vibration of Ti-O and Fe-
O bands.[3] Moreover, the high electronegativity
positions of C=O and -O- groups disappeared at
1735 and 1080 cm-1, respectively. Thus, the Ti4+ and
Fe3+ ions were chemical interacted with these groups
and growth to the crystal phase on GA structure.[13]
first-order model.
Ln CC = − kt
(2)
o
t
where k (min-1) is the reaction rate constant; and t is
irradiation time.
For cyclic tests, the catalytic after degradation
process was separated and washed using ethanol to
remove MB residual and heated at 120 °C for 2 h.
3. RESULTS AND DISCUSSION
3.1. Characterization
Vietnam Journal of Chemistry
Nguyen Huu Hieu et al.
Figure 1: XRD patterns of GA, TiO2/GA,
Figure 2: FTIR spectra of GA, TiO2/GA,
and Fe2O3-TiO2/GA
and Fe2O3-TiO2/GA
The surface morphologies of materials are TiO2/GA was observed because of the effect by
investigated by SEM imaging as indicated in Figure electrostatic force between the negatively charged of
3. The rGO sheets were self-assembled to form residual oxygen-containing groups in rGO and
framework due to hydrogen bonds, hydrophobic and positively charged of Fe3+ and Ti4+ ions.[14] This is in
π–π interactions. For TiO2/GA and Fe2O3-TiO2/GA, a good convention with XRD and FTIR data.
the anchormen of particles were uniform on GA
The EDX result of Fe2O3-TiO2/GA was
structure, increasing the surface area and number of performed to identify the chemical compositions of
active sites of the material. This result confirmed the composite. The present of Ti and Fe elements were
distribution of Fe2O3-TiO2/GA as shown in figure 4. recorded, indicating the anchoring of TiO2 and
Moreover, the reduction of particles size in Fe2O3- Fe2O3 particles in GA.
(a)
(b)
(c)
Figure 3: SEM images of (a) GA, (b) TiO2/GA, and (c) Fe2O3-TiO2/GA
Figure 4: Elemental mapping of Fe2O3-TiO2/GA
Vietnam Journal of Chemistry
Materials
Synthesis of Fe2O3/TiO2/graphene…
Table 2: The elemental compositions in materials
Elements (wt.%)
C
76.81
53.88
39.02
O
Ti
-
Fe
-
GA
TiO2/GA
23.19
18.85
33.74
27.27
-
Fe2O3-TiO2/GA
19.56
7.68
The Raman spectra of materials display two functional and disordered sites in graphene-based
characteristic modes at 1335 and 1596 cm-1 with materials.[15] The ID/IG value of Fe2O3-TiO2/GA is
respect to the D and G-bands as shown in Figure 5a. 1.25, which is higher comparing to that of TiO2/GA
The D-band is characterized by the crystalline (ID/IG = 1.18) and GA (ID/IG = 1.14). The number of
defects and G-band is assigned to the sp2-hybridized bonds between Fe2O3, TiO2 particles and GA were
carbon atoms in the carbon network. The intensity higher than GA, indicating the good incorporation of
ratio of these peaks (ID/IG) reflected the degree of the particles with the GA.[16]
(a)
(b)
Figure 5: (a) Raman spectra of GA, TiO2/GA, and Fe2O3-TiO2/GA;
(b) UV-Vis spectra of TiO2/GA and Fe2O3-TiO2/GA
Besides, the absorption bands of TiO2/GA and enhancing the absorption of light irradiation and
Fe2O3-TiO2/GA were shifted to the visible region, improving the photo-activity for the removal of
expanding to a longer wavelength than of TiO2 as organic dyes.[17]
shown in figure 5b. The band-gap energies of the
composites were calculated from Kubelka-Munk
equation were found to be 2.63 (TiO2/GA) and 2.08
eV (Fe2O3-TiO2/GA) which are smaller than of TiO2
(3.2 eV). The band gap of composites decreased
which shows the formation of bonds between the
particles and carbon network of GA.[17] This result
confirmed the effect of GA on the distribution of
particles increase number of nuclating sites, leading
to the formation of smaller particles size and
expensing in the efficiency of light absorption.[3] The
presence of Fe2O3 acts as a co-sensitizer to enhance
the number of photo-generated electrons and holes
in the Fenton reaction.[18] The Fe2O3 and TiO2
particles were successfully formed and evenly
distributed on GA substrate to form Fe2O3-TiO2/GA,
3.2. Photocatalytic performance
Figure 6 shows the Fenton-photocatalytic of TiO2,
TiO2/GA, and Fe2O3-TiO2/GA at different
irradiation times. It is clear that the residual
concentration of MB in solution obviously decreases
with enhancing the time. The removal efficiencies of
TiO2/GA and Fe2O3-TiO2/GA are about 76.52 and
97.38 %, respectively, which are higher than that of
TiO2 (H = 55.69 %) after 60 min of UV-light
irradiation. For the Fe2O3-TiO2/GA, the degradation
rate rapidly accelerated within 10 min and the MB
dye almost vanished after 40 min in the present of
Fe2O3-TiO2/GA.
Vietnam Journal of Chemistry
Nguyen Huu Hieu et al.
Figure 6: Effect of irradiation time on the MB
degradation performance of TiO2, TiO2/GA, and
Fe2O3-TiO2/GA
Figure 7: Pseudo-first-order kinetic plots
of the MB degradation
The pseudo-first-order model applied to radicals interacted and degraded MB dye.[6,7]
examine the degradation kinetic of materials and the
Table 3: The parameters for pseudo-first-order
linear plots were presented in figure 7. The plots are
in straight line with the negative slope value. The
parameters of linear pilots are showed in table 3.
The degradation process is highly suitable the
pseudo-first-order model for high correlation
coefficients (R2 > 0.90). The values of rate constant
of photocatalytic samples are 0.0558, 0.0228, and
0.0131 min-1 corresponding to the Fe2O3-TiO2/GA,
TiO2/GA, and TiO2, respectively. The phenomenon
could be ascribed to the synthesized composites with
the distribution of particles in GA, preventing the
agglomeration particles and increasing more number
of active sites in the composite. The role of electron
conduction in GA network promotes the migration
efficiency of photo-generated electrons-hole pairs,
thus the degradation activities of composites are
higher than that of TiO2.[19]
degradation kinetic model
Materials
Fe2O3-TiO2/GA
TiO2/GA
k (min-1)
0.0558
0.0228
0.0131
R2
0.9608
0.9273
0.9819
TiO2
On the other hand, GA substrate plays a crucial
role in the photocatalytic degradation of Fe2O3-
TiO2/GA by cooperation effects between adsorption
and Fenton reaction.[14] The interconnected network
and functional groups of GA was favorable for the
formation of electrostatic and π-π interactions with
MB, leading to the enrichment of MB molecular in
the composite. Thus, the MB concentration in the
composite increased and the contact abilities of
particles with MB adsorbed were also advanced,
accelerating the Fenton oxidation reaction to
degrade the pollutants. Besides, the evenly
distribution of particles in GA provides the more
active sites and generate photo-excited electron–hole
pairs.[22] Moreover, GA transferred the charge
carriers between TiO2 and Fe2O3 particles, reducing
the electron-hole recombination, resulting in the
prolong life time electron-hole pair and advancing
the removal performance.[3]
The removal performances of synthesized
materials are compared with other materials from
other studies which are presented in Table 4. The
superior characteristics of Fe2O3-TiO2/GA indicated
that the photo-generated electron-hole pairs
separation between the band gap of Fe2O3 and TiO2,
expanding the solar light absorption region of
material. Under light irradiation, the electron placing
in the valence band of TiO2 is stimulated and shifted
to conduction band with ease, which leads to the fact
that the interfacial electron hole is separated. The
The reusability of Fe2O3-TiO2/GA was also
tested to evaluate the heterogeneous Fenton catalysts
as shown in figure 8. The degradation performance
still remained over 80 % after 5 cycles. This result
proved the catalysis has an excellent reusability in
photodegradation activity.
−•
holes reacted with water molecules to generate O2
radical. The photo-excited electron transferred to the
conduction band of Fe2O3 is converted to Fe2+ from
Fe3+ through the reduction reaction. Then, the
Fe2+/Fe3+ pair reacted with H2O2 to produce the
•OOH and via Fenton. The reactive oxidation
Vietnam Journal of Chemistry
Synthesis of Fe2O3/TiO2/graphene…
Table 4: The removal performance of graphene-based materials
Materials
Conditions
Removal efficiency (%)
97.38
References
This work
Fe2O3-TiO2/GA 20 mg of photocatalyst, 20 mL of MB
(50 mg/L), 2 mL of H2O2, irradiation
time of 60 min, 25 W UV lamp
TiO2/GA
20 mg of photocatalyst, 20 mL of MB
(50 mg/L), 2 mL of H2O2, irradiation
time of 60 min, 25 W UV lamp
20 mg of photocatalyst, 20 mL of MB
(50 mg/L), 2 mL of H2O2, irradiation
time of 60 min, 25 W UV lamp
50 mg of photocatalyst, 100 mL of MB
(10 mg/L), irradiation time of 90 min,
100 W tungsten lamp
100 mg of photocatalyst, 400 mL of MB
(40 mg/L), H2O2 (1.10 mM), irradiation
time of 70 min, 100W high-pressure
mercury lamp
76.52
55.69
97.00
96.0
This work
This work
[20]
TiO2
α-Fe2O3/rGO
α-Fe2O3/GO
[21]
ZnO-
Fe3O4/rGO
20 mg of photocatalyst, 50 mL of MB
(10 mg/L), 30 µM of H2O2, irradiation
time of 150 min, 300 W UV Xe lamp
97.0
[22]
recombination, leading to the elevation of
photocatalysis activity. The degradation data were
well fitted to pseudo-first-order kinetic model.
Accordingly, Fe2O3/TiO2/GA could be concerned as
an efficient Fenton-photocatalysis for the
degradation of dye from water.
Conflict of interest. The authors declare that they
have no competing interests.
Acknowledgments. This research is funded by Ho
Chi Minh City University of Technology, VNU-
HCM, under grant number T-PTN-2019-46. We
acknowledge the support of time and facilities from
Ho Chi Minh City University of Technology
(HCMUT), VNU-HCM for this study.
Figure 8: Stability of the Fe2O3-TiO2/GA composite
in the removal of MB
4. CONCLUSION
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Corresponding author: Nguyen Huu Hieu
VNU-HCM Key Laboratory of Chemical Engineering
and Petroleum Processing (CEPP Lab)
Ho Chi Minh City University of Technology
268, Ly Thuong Kiet street, district 10, Ho Chi Minh City 70000, Viet Nam
E-mail: nhhieubk@hcmut.edu.vn.
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