Constructing an Acidic Microenvironment by MoS2 in Heterogeneous Fenton Reaction for Pollutant Control

Article abstract of DOI:10.1002/anie.202105736

Although Fenton or Fenton-like reactions have been widely used in the environment, biology, life science, and other fields, the sharp decrease in their activity under macroneutral conditions is still a large problem. This study reports a MoS₂ cocatalytic heterogeneous Fenton (CoFe₂O₄/MoS₂) system capable of sustainably degrading organic pollutants, such as phenol, in a macroneutral buffer solution. An acidic microenvironment in the slipping plane of CoFe₂O₄ is successfully constructed by chemically bonding with MoS₂. This microenvironment is not affected by the surrounding pH, which ensures the stable circulation of Fe³⁺/Fe²⁺ on the surface of CoFe₂O₄/MoS₂ under neutral or even alkaline conditions. Additionally, CoFe₂O₄/MoS₂ always exposes “fresh” active sites for the decomposition of H₂O₂ and the generation of ¹O₂, effectively inhibiting the production of iron sludge and enhancing the remediation of organic pollutants, even in actual wastewater. This work not only experimentally verifies the existence of an acidic microenvironment on the surface of heterogeneous catalysts for the first time, but also eliminates the pH limitation of the Fenton reaction for pollutant remediation, thereby expanding the applicability of Fenton technology.

Full text of DOI:10.1002/anie.202105736

A Journal of the Gesellschaft Deutscher Chemiker
Angewandte
International Edition Chemie
www.angewandte.org
Accepted Article
Title: Constructing an Acidic Microenvironment by MoS2 in
Heterogeneous Fenton Reaction for Pollutant Control
Authors: Qingyun Yan, Cheng Lian, Kai Huang, Lihong Liang, Haoran
Yu, Pengcheng Yin, Jinlong Zhang, and Mingyang Xing
This manuscript has been accepted after peer review and appears as an
Accepted Article online prior to editing, proofing, and formal publication
of the final Version of Record (VoR). This work is currently citable by
using the Digital Object Identifier (DOI) given below. The VoR will be
published online in Early View as soon as possible and may be different
to this Accepted Article as a result of editing. Readers should obtain
the VoR from the journal website shown below when it is published
to ensure accuracy of information. The authors are responsible for the
content of this Accepted Article.
To be cited as: Angew. Chem. Int. Ed. 10.1002/anie.202105736
Link to VoR: https://doi.org/10.1002/anie.202105736

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
Constructing an Acidic Microenvironment by MoS
Heterogeneous Fenton Reaction for Pollutant Control
2
in
‡
‡
Qingyun Yan , Cheng Lian , Kai Huang, Lihong Liang, Haoran Yu, Pengcheng Yin, Jinlong Zhang, and
Mingyang Xing*
by Fe2+ and produces a large number of hydroxyl radicals (•OH),
which is typical reactive oxygen species (ROS) that
Abstract: Although Fenton or Fenton-like reactions have been widely
used in the environment, biology, life science and other fields, the
sharp decrease in their activity under macroneutral conditions is still
a
indiscriminately attacks organic molecules. Unfortunately, the
Fenton reaction has not truly overcome its pH limitation and is
only applicable under acidic conditions. Although heterogeneous
Fenton techniques are considered to be able to degrade organics
under neutral conditions, most reported heterogeneous Fenton
techniques focus on the initial pH (pHinitial) of the reaction
solution.[3] However, the pH of the system often changes from
neutral to acidic during or after the Fenton reaction.[4] If the pH of
the system is kept neutral by using a buffer solution, the activity
of the heterogeneous Fenton reaction to degrade organic matter
is extremely reduced.[5] This result is mainly because when the pH
is close to neutral, Fe2+ will react with OH¯ to precipitate iron
oxides, such as iron hydroxide, resulting in the formation of iron
sludge and a sharp decrease in the decomposition efficiency of
a large problem. This study reports a MoS
Fenton (CoFe /MoS ) system capable of sustainably degrading
organic pollutants, such as phenol, in a macroneutral buffer solution.
An acidic microenvironment in the slipping plane of CoFe is
successfully constructed by chemically bonding with MoS . This
microenvironment is not affected by the surrounding pH, which
2
cocatalytic heterogeneous
2
O
4
2
2
O
4
2
3
+
2+
ensures the stable circulation of Fe /Fe on the surface of
CoFe
CoFe
2
O
O
4
/MoS
/MoS
2
under neutral or even alkaline conditions. Additionally,
2
4
2
always exposes "fresh" active sites for the
1
decomposition of H
2
O
2
and the generation of O
2
, effectively inhibiting
the production of iron sludge and enhancing the remediation of
organic pollutants, even in actual wastewater. This work not only
experimentally verifies the existence of an acidic microenvironment
on the surface of heterogeneous catalysts for the first time but also
eliminates the pH limitation of the Fenton reaction for pollutant
remediation, thereby expanding the applicability of Fenton technology.
2 2
H O . Furthermore, the oxidation potential of •OH under neutral
conditions decreases, greatly decreasing its oxidation capacity.
However, acidic reaction conditions not only corrode equipment
but also increase the reaction cost, which is not conducive to the
large-scale promotion of Fenton technology. Therefore, the
development of heterogeneous Fenton reaction systems that can
truly overcome the pH limitation has important scientific
significance in the field of environmental pollution control.
Introduction
The Fenton reaction has been developed and improved for more
than 100 years[1] and continues to be an irreplaceable reaction in
pollutant control, especially in the remediation of refractory
organic pollutants.[2] During the Fenton reaction, H
In this paper, we chemically compound commercial cobalt
2
O
2
is activated
2 4 2
ferrite (CoFe O ) and MoS nanosheets together through a facile
one-pot hydrothermal method. The resulting material
demonstrates outstanding phenol degradation under either acidic
or pH ≈ 7.0 macroneutral buffer conditions. The introduction of
[
*]
Dr. Q.Y. Yan, L.H. Liang, H.R. Yu, Prof. Dr. J.L. Zhang, Prof. Dr.
M.Y. Xing
2
MoS can realize the self-adjustment of the Fenton system from
Key Laboratory for Advanced Materials and Joint International
Research Laboratory of Precision Chemistry and Molecular
Engineering, Feringa Nobel Prize Scientist Joint Research Center,
Frontiers Science Center for Materiobiology and Dynamic
Chemistry, Institute of Fine Chemicals, School of Chemistry and
Molecular Engineering, East China University of Science and
Technology
basic to acidic without the addition of acid. X-ray photoelectron
spectroscopy (XPS), Zeta potential tests, Fourier transform
infrared (FT-IR) spectroscopy and density functional theory (DFT)
calculations demonstrate that the prepared composite catalyst
(
CoFe
retaining an acidic microenvironment even in a neutral buffer.
Thus, the CoFe /MoS -based heterogeneous Fenton system
2 4 2
O /MoS ) can maintain a stable iron cycle on its surface by
130 Meilong Road, Shanghai 200237 (China)
E-mail: mingyangxing@ecust.edu.cn
Prof. Dr. J.L. Zhang, Prof. Dr. M.Y. Xing
Shanghai Engineering Research Center for Multi-media
Environmental Catalysis and Resource Utilization, East China
University of Science and Technology
2
O
4
2
can truly overcome the pH limitation and realize the efficient
removal of phenol even from actual industrial wastewater under
constant macroneutral conditions. The oxidation performance of
130 Meilong Road, Shanghai 200237 (China)
2 4 2
the CoFe O /MoS system is not only much better than that of a
Prof. Dr. C. Lian, Dr. K. Huang
State Key Laboratory of Chemical Engineering, Shanghai
Engineering Research Center of Hierarchical Nanomaterials,
School of Chemistry and Molecular Engineering, East China
University of Science and Technology
CoFe
2
O
4
system but also significantly better than the activity of a
2+
2 2
traditional homogeneous Fenton (Fe /H O ) system.
130 Meilong Road, Shanghai 200237 (China)
Dr. P.C. Yin
Results and Discussion
BCEG Environmental Remediation Co., LTD.
NO.6 of Jingshun East St., Chaoyang Dist., Beijing (China)
Supporting information for this article is given via a link at the end of
the document.((Please delete this text if not appropriate))
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
Figure 1. (a) Schematic illustration showing the preparation of CoFe
2
O
4
/MoS
2
. (b) Picture of the mass preparation of catalysts (20 grams of powder can be obtained
2 4 2 2 4 2 2 4 2 2 4 2
at one time). (c) XRD spectra of CoFe O , MoS , and CoFe O /MoS . (d) SEM image of CoFe O /MoS . (e) TEM and HRTEM images of CoFe O /MoS .
Synthesis and structure of CoFe
procedure of CoFe /MoS is briefly summarized in the
schematic diagram of Figure 1a. After a facile hydrothermal and
impurity removal process, CoFe and MoS nanosheets were
successfully combined. CoFe or MoS on their own was
2
O
4
/MoS
2
. The synthesis
2
indicate that the lattice fringes of MoS are classically curved
2
O
4
2
strips, while the lattice spacing of 0.62 nm is attributed to the (002)
crystal plane, which is consistent with previous reports.[6] Not
surprisingly, the lattice fringes of CoFe
along the edges of the MoS nanosheets. Lattice spacings of 0.25
nm, 0.30 nm, and 0.49 nm represent the (311), (220), and (111)
crystal planes of CoFe
, respectively.[7] Interestingly, both the
SEM and TEM images show that the CoFe nanoparticles are
mainly dispersed at the chamfered edge of the MoS nanosheets,
and the flaky surface of MoS remains smooth after loading
CoFe (Figure 1d). More SEM images, as shown in Figure S2,
indicate that many nanoparticles aggregate on the side edges
formed by the stacked MoS nanosheets. This result suggests
that the Mo or S atoms at the edge of MoS are for the most part
chemically bonded with CoFe , which may play a key role in
the construction of an acidic microenvironment on the surface
2 4
O are also observed
2
O
4
2
2
2
O
4
2
hydrothermally prepared in the absence of one or the other for
comparison experiments. It is easy to realize the mass production
of this catalyst by using a one-step hydrothermal synthesis
strategy (Figure 1b). As shown in Figure 1c, the characteristic
2
O
4
2
O
4
2
peaks of CoFe
2
O
4
and MoS
2
can be observed in the XRD spectra
and MoS are
2
2
O
4
of CoFe /MoS
2
O
4
2
, suggesting that CoFe
2
O
4
2
successfully chemically compounded together. The details are
analyzed in Supporting Information. It is worth mentioning that the
2
appearance of the peak of 20-25 degrees in CoFe
CoFe /MoS may be caused by surface oxidation in the
hydrothermal process compared with commercial CoFe
Figure S1).
The CoFe
easily observed in the SEM image of Figure 1d. To understand
the microstructure of CoFe /MoS , TEM and HRTEM were
employed to characterize the catalyst, as shown in Figure 1e. The
adhesion of the MoS nanosheets to the CoFe nanoparticles
can be clearly observed. MoS exhibits a classic flake-like
structure, and CoFe has a size of 30 ~ 50 nm. HRTEM images
2
4
O and
2
O
4
2
2
O
4
2
2
O
4
because it is known that unsaturated S at the edge of MoS
proton-bonding properties.[8]
2
has
(
2
4 2
O particles loaded on MoS nanosheets can be
Degradation of phenol at different initial pH values. To
comprehensively investigate the performance of CoFe /MoS
in decomposing H and degrading organic pollutants, we first
O
4
2
2
O
4
2
2
2
O
2
carried out an experiment on the degradation of phenol under
acidic conditions (pH ≈ 4.0). The adsorption curve of phenol
shows that the intrinsic adsorption of phenol by the catalysts can
2
2 4
O
2
2
O
4
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
be ignored (Figure S3). The phenol degradation activity of
2 4
CoFe O is improved by hydrothermal treatment, but the
magnitude is negligible, and the degradation efficiency of
hydrothermal-treated CoFe
% within 25 min (Figure 2a). When MoS
representing a physical mixture of CoFe
2
O
4
-activated H
2
O
2
on phenol is only
5
2
is added to the system,
2
O
4 2
and MoS , the
degradation rate of phenol (16%) slightly improves. It is surprising
that CoFe /MoS exhibits a 100% degradation rate of phenol
2
O
4
2
within 25 min, which is significantly higher than that of all
previously mentioned reference samples. This difference in
performance of catalysts obtained by physical or chemical
methods is a point of concern and discussion, indicating that the
2 4 2
chemical attraction between CoFe O and MoS plays an
important role in the Fenton reaction.
The influence of various objective factors on degradation
efficiency has been systematically studied, such as the ratio of
Figure 2. (a) Phenol degradation behavior of different catalysts at pHinitial
.0. (b) Degradation of phenol at different initial pH values. (c) Trend curve of
phenol degradation and the corresponding pH of CoFe O /MoS at an initial
≈
MoS
discussion is in Figure S4~7). Unlike the traditional homogeneous
Fenton reaction, the phenol degradation rate of CoFe /MoS
increases (Figure S7b), indicating that the utilization efficiency of
steadily increases and showing that the catalyst lifts the
restriction on H utilization. Using the above results, the optimal
reaction conditions are as follows: to 100 mL of water containing
2 2 4 2 2
to CoFe O , the catalyst dose and the H O dose (detailed
4
2
4
2
pH ≈ 7.0. (d) The phenol decay trend in different iron oxides/MoS
heterogeneous Fenton systems under different initial pH condition. ([phenol]
20 mg/L, [Catalyst] = 30 mg, [H ] = 500 μL).
2
based
2
O
4
2
=
2 2
O
2 2
H O
2
O
2
by the short lifetime of ROS, and on the other hand, it may be
caused by a mutual conversion between different ROS.[10]
2
0 mg/L phenol, we added 30 mg of catalyst at a Mo/Fe ratio of
.2 and 500 µL of H
In addition, CoFe
2
O
4
/MoS
2
exhibits outstanding pHinitial
0
2
2
O .
adaptability, showing similar phenol degradation performance
even at pHinitial ≈ 7 and pHinitial ≈ 9 (Figure 2b). This result is also
considered to be one of the advanced features of this
2
In our previous works, it was found that MoS could promote
the conversion of Fe3+ to Fe . There is significant iron leaching
2+ [9]
in the CoFe
detected in the blank CoFe
indicates that the chemical state of CoFe
stable even under acidic conditions, but the introduction of MoS
can significantly change the chemical state of CoFe on the
surface. Regarding the CoFe /MoS
system, the Fe2+
2
O
4
/MoS
2
-based Fenton system, while no iron is
system (Figure S8). This result
on the surface is very
heterogeneous Fenton system compared to traditional
homogeneous Fenton systems (Figure S12).[3c] In our case, when
2
O
4
2
O
4
the pHinitial of a solution containing pollutants is adjusted to neutral,
2
2 4 2
the addition of CoFe O /MoS causes the pH to approach
2
O
4
3.0~4.0; that is, the acidic nature of the catalyst causes the actual
2
O
4
2
pH to deviate from the predetermined value; however, an
excellent degradation rate of pollutants is maintained (Figure 2c).
It has been demonstrated that the pH change of the system
concentration increases at 1 min and thenfluctuates in equilibrium
at a higher level, indicating that the metal active site of ≡Mo4+
exposed on the MoS
ions on the CoFe
3.3 mg/L (Figure S8), which is consistent with the value (13.4
2
surface still promotes the circulation of iron
2
originates from the existence of MoS (Figure S13), which further
O
4
surface. The Fe2+ concentration at 25 min is
2
affects the degradation characteristics. The modification strategy
proposed by us is also applicable to other heterogeneous Fenton
systems. As shown in Figure 2d, the iron oxides chemically
1
mg/L) measured by the Inductively Coupled Plasma Atomic
Emission Spectrometer (Table S1). Fe2+ can easily escape from
the catalyst surface into the solution under acidic conditions and
bonded with MoS
2
show excellent degradation activity of phenol.
/MoS Fenton system automatically adjusts
Because the CoFe
2
O
4
2
2 2
then activate the widespread dispersion of H O for eliminating
the environment to an acidic pH, we investigated the degradation
mechanism of phenol at pHinitial ≈ 4.0 (Figure S14). Compared with
the homogenous Fenton system, the intermediate products
target pollutants with redox reactions in a short time. Furthermore,
ROS quenching experiments were carried out to preliminarily
determine the active species in the CoFe
2
O
4
/MoS
2
-based Fenton
2 4 2
generated by the degradation of phenol in the CoFe O /MoS -
1
system (Figure S9 and S10). The results indicate that O
2
plays a
based heterogeneous Fenton system are significantly reduced,
reducing the risk of producing toxic byproducts. The acid-
key role in the whole degradation reaction. Electron paramagnetic
resonance (EPR) can further qualitatively reflect the contribution
regulating nature of MoS
CoFe /MoS -based Fenton system can truly overcome the pH
limitation.
2
makes it difficult to see whether the
2 4
of ROS. Compared with the CoFe O system, the signal of
2
O
4
2
DMPO•-O −
(DMPO: 5,5-dimethyl-1-pyrrolidine-N-oxide) is
2
1
weaker, but the signals of DMPO•-OH and TEMP- O
2
are
Degradation of phenol in a neutral buffer solution. To
investigate the Fenton activity of the catalyst in a neutral reaction
system, we changed the solvent to a mixed phosphate buffer to
ensure a stable pH of 6.86 throughout the reaction. Figure 3a
2 4 2
enhanced in the CoFe O /MoS system under uniform acidic
conditions (Figure S11a-c). On the one hand, this result is caused
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
2 4 2
the surface cover the active sites of CoFe O /MoS . This
phenomenon can be alleviated after the addition of ultraviolet light,
which can be regarded as an effective means to restore the
activity of the catalyst. The RhB degradation performance of
2 4 2
CoFe O /MoS is restored and continues to run for the next five
cycles after the solution is irradiated at 365 nm wavelength for a
period of time. This result is because ultraviolet light can
effectively remove carbon deposition on the surface of the
catalyst[11] and inhibit catalyst poisoning. The continuous and
2 4 2
effective degradation activity of CoFe O /MoS in the buffer
solution implies that it has the potential to treat actual industrial
wastewater.
Different from the EPR results under acidic conditions (Figure
S11a), it is difficult to detect the •OH signal in a neutral buffer
1
solution (Figure S17a). However, the EPR signal of O
2
can still
Figure 3. Degradation behavior of the CoFe
in a neutral buffer solution (pH = 6.86, [Catalyst] = 30 mg, [H
a) Phenol decay trend and the corresponding pH change ([phenol] = 20
mg/L). (b) Degradation rate of antibiotics, phenolics, and dyes ([Enro, TH, Nor,
phenol, RhB, MB, NC] = 20 mg/L, [4-CP, BPA] = 10 mg/L). (c) Stability of the
2
O
4
/MoS
2
-based Fenton reaction
−
be detected in Figure S17b. The capture effect of DMPO on •O
2
2
O
2
] = 500 μL):
generally occurs in methanol and other alcohol phase solutions
during the EPR test. However, the solubility of disodium hydrogen
phosphate-sodium dihydrogen phosphate buffer in an alcohol
phase solvent is extremely low, causing the absence of
corresponding EPR data. As expected, ROS quenching
(
2 4 2
CoFe O /MoS -based Fenton reaction for the degradation of RhB ([RhB] = 20
mg/L; The recovered samples were pretreated with UV irradiation only before
the Fenton reaction). (d) Degradation curves of RhB under different conditions
in the presence of different radical scavengers, including TBA, BQ, and TEMP
experiments show that 1
2
O is the main active species of the
(
[RhB] = 20 mg/L, [TBA] = 2 mL, [BQ] = 15 mg, [TEMP] = 200 μL).
CoFe
2
O
4
/MoS
2
-based Fenton system in a neutral buffer solution
1
(
Figure 3d). Compared with •OH, O
migration distance under neutral conditions. Therefore, 1
2
has a longer lifetime and
is
illustrates the phenol degradation decay trend and pH changes of
the catalyst in the macroneutral buffer. The continuous phenol
degradation in the macroneutral buffer shows that the adsorption
O
2
more conducive to realizing the long-term degradation of organic
pollutants by Fenton or Fenton-like reactions.[10b] In previous
efforts of researchers, a conclusion was reached that the active
species of a heterogeneous Fenton system under neutral
conditions is high-valent iron.[12] In this case, sulfoxides were used
as a unique indicator for the detection of high-valent iron (Fe(IV))
to determine the active species in the system (Figure S18).[13] As
a result, Fe(IV) does not play a major role in the decay of
effect of CoFe
4 h, the phenol degradation rate of only CoFe
degradation is also negligible (5.1%) in the physically mixed
system of CoFe + MoS . The effective activation of H by
CoFe /MoS can be achieved in the buffered system, which is
specifically reflected in the high degradation rate (> 70%) within
0 h. Due to the offsetting effect of the macroneutral buffer, the
2
O
4
/MoS
2
on phenol is negligible. After reacting for
2
2 4
O
is 6.2%. Phenol
2
O
4
2
2 2
O
2
O
4
2
1
phenol.[14] In other words, the CoFe
2 4 2
O /MoS -based Fenton
pH of the entire reaction is in a constant state, which can be called
a true neutral condition.
reaction is still dominated by the activation of H
O
2 2
for the
1
production of O
2
.
To verify the general applicability of the oxidation system in a
macroneutral buffer environment, different environmental
pollutants, such as antibiotics (enrofloxacin (Enro), tetracycline
hydrochloride (TH), and norfloxacin (Nor)), phenols
Treatment of actual wastewater and the design of an
automated reactor. It is well known that the advanced treatment
of wastewater is always one of the biggest problems in the field
2 4 2
of water pollution control. We used CoFe O /MoS as the Fenton
(
tetrachlorophenol (4-CP), bisphenol A (BPA), and phenol) and
dyes (rhodamine B (RhB), methylene blue (MB), and new coccine
NC)), were selected as the target pollutants to evaluate the
activity of the CoFe /MoS -based Fenton system. As expected,
the CoFe /MoS system demonstrates excellent degradation
activity for all organic contaminant molecules, as shown in Figure
b and Figure S15. Moreover, the reaction rate can be further
accelerated by increasing the amount of H , and its reaction
catalyst for removing the chemical oxygen demand (COD) in
actual wastewater (soil remediation wastewater from Beijing
Construction Engineering Group Co., LTD., main component:
nitrobenzoates) under neutral conditions to explore its practical
application value. During the first run, the COD of the actual
wastewater decreases from 428 mg/L to 153 mg/L within 2 h,
which is accomplished without adjusting the pH; additionally, the
system maintains outstanding cycling stability, as illustrated in
Figure 4a. Specifically, the COD removal rate over five cycles is
maintained at 58.2~67.5% (After 3 cycles, the pH of the whole
reaction remained at about 6.8), greatly proving that
(
2
O
4
2
2
O
4
2
3
2
O
2
efficiency is even significantly better than that of the traditional
homogeneous Fenton reaction system (Figure S16). The long-
term cycling test is shown in Figure 3c, which shows that the RhB
2 4 2
degradation performance of CoFe O /MoS decreases after five
2 4 2
CoFe O /MoS provides an excellent advantage in the advanced
testing cycles; however, it still remains at an acceptable level. This
result is mainly because the excess dye molecules adsorbed on
treatment of wastewater. Furthermore, the SEM, XRD, and XPS
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
Figure 4. Application scenarios of the CoFe
2
O
4
/MoS
2
-based Fenton reaction system: (a) Activity and stability of the CoFe
2
O
4
/MoS
2
-based Fenton system for the
treatment of actual wastewater without adjusting the pH (soil remediation wastewater with an original COD of 428 mg/L, [Catalyst] = 50 mg, [H
7.0, reaction time of 2 h). (b) Comparative photo of the magnetic separation of reduced iron powder and CoFe /MoS after the degradation of actual
wastewater. (c) Melamine sponges loaded with CoFe /MoS . (d) Design of an automated reactor for the degradation of simulated organic pollutants (V[L-RhB]
.0 L, [L-RhB] =10 mg/L, [H ] = 5.0 mL, flow rate: 100 mL/min).
2 2
O ] = 800 μL, pH
≈
2
O
4
2
2
O
4
2
=
5
2 2
O
tests of the CoFe
2
O
4
/MoS
2
sample after cycling performance also
solution. The oxidation reaction occurs when the L-RhB solution
proved its stability (Figure S19 and S20). On the other hand, the
generation of iron sludge has always been a key problem limiting
the large-scale application of Fenton or Fenton-like reactions in
the environment. For instance, when commercial reduced iron
powder is used as a Fenton catalyst to treat actual wastewater, a
large amount of iron sludge is produced after the reaction (left of
2 2
with H O meets the catalyst sponges in the catalytic device tower
at a flow rate of 100 mL/min (Supplementary Video 1). It can be
seen from the enlarged picture of the catalytic unit generating
tower that the color of the simulated polluted wastewater gradually
changes from the original fresh peach color to nearly colorless in
the direction of the water flow in this unit, indicating that the
oxidation reaction occurs (Figure S22). It is worth mentioning that
the adsorption of L-RhB by sponges is excluded (Figure S23). As
neutral wastewater flows through the catalyst sponges, the pH of
the solution drops to 3.0~4.0, owing to the presence of
2 4 2
Figure 4b), while the ferromagnetic CoFe O /MoS system
presents a transparent solution after the Fenton reaction in the
presence of a magnet (right of Figure 4b). The hysteresis loop
also proves the magnetic properties of the CoFe
2
O
4
/MoS
2
(Figure
S21). Based on the above certification, CoFe
2
O
4
/MoS
2
can not
2 4 2
CoFe O /MoS . After the wastewater is treated and passes
only reduce the generation of iron sludge but can also be simply
recovered from the system due to its ferromagnetic
characteristics.
through the aluminium oxide filled tower, its pH automatically
returns to 7.0 (Figure 4d), mainly because aluminium oxide is an
amphoteric oxide. The color of the effluent solution is transparent,
and the degradation rate of L-RhB reaches 100%. The trial
operation of the pilot device demonstrates the possibility of its use
for directly treating industrial wastewater under neutral conditions;
furthermore, no additional reagents are needed to adjust the pH,
greatly decreasing the operating cost. Furthermore, the flow rate
of the pilot device also shows its high promise for use in a
production device.
A pilot device was built to further test the practical application
2 4 2
value of CoFe O /MoS . The pre-preparation work was as follows:
a large number of 1 cm × 1 cm × 1 cm melamine sponges were
immersed in 1.0 L of aqueous solution with 5.0 g of dispersed
CoFe
0 min and dried at 200 °C for 2 h to obtain the catalyst sponges
Figure 4c). As shown in the flowchart interpretation in Figure 4d,
2 4 2
O /MoS powder. This solution was then ultrasonicated for
3
(
the device consists of a simulated wastewater container under
neutral conditions using tap water (pHinitial ≈ 7.0), and a catalytic
unit generating tower is filled with catalyst sponges. A pH
adjustment tower is filled with aluminium oxide, which is
successively connected with a receiving container for the treated
wastewater, a drying tower and a vacuum pump from left to right.
Mechanism Investigation. To understand the specific
reaction process at the heterogeneous catalyst interface, we first
2 4 2
tested the dissolution of iron ions from CoFe O /MoS in a neutral
buffer solution. Because Fe3+ has poor water solubility under
neutral conditions, almost no free Fe3+ is detected. Interestingly,
in the neutral buffer solution, the trend of the Fe2+ concentration
dissolved in water is completely different from that under acidic
2 2
Then, 5.0 mL of 30% H O was mixed with the simulated
Lissamine rhodamine B (L-RhB) pollutant to obtain a uniform
2 4 2
conditions (Figure 5a and Figure S8). In the CoFe O /MoS
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
system (Figure 5a), the concentration of Fe2+ decreases from 3.09
concentration indicates the increase of active sites on the surface
mg/L to 0.61 mg/L within 2 min as the reaction takes place and
2 4 2
of CoFe O /MoS .
finally stabilizes at 0.33 mg/L. The addition of H
2
O
2
has little effect
is not the main reason
for the dissolution of iron ions. In contrast, the dissolution of Fe2+
is not detected in either the pure CoFe system or the physically
mixed system (CoFe + MoS ), indicating that the chemical
interaction between MoS and CoFe significantly changes the
surface chemical state of CoFe and triggers a series of
XPS was performed to understand the elemental composition
and chemical state of the sample surface to a certain extent. The
2
+
2 2
on the variation of Fe , indicating that H O
2 4
high-resolution Fe 2p XPS spectrum of CoFe O can be split into
2
O
4
six peaks, as shown in Figure 5b, and the peaks at 732.74 and
718.01 eV are satellite peaks. The peaks at 723.06 eV and 709.82
eV are attributed to Fe(II) 2p1/2 and Fe(II) 2p3/2, respectively,
and the peaks at 725.45 and 712.00 eV belong to Fe(III) 2p1/2
2
O
4
2
2
2 4
O
2
O
4
Fenton-like reactions. In fact, for heterogeneous Fenton reactions, and Fe(III) 2p3/2, respectively. The relative content of ≡Fe2+ on
the ≡Fe2+ site exposed on the surface of the catalyst is the active
the surface of CoFe increases after compounding with MoS
site for decomposition of H Notably, the splitting peak at 706.75 eV is due to the presence of
.Therefore, the increase of Fe2+
2
O
4
2
.
2
O
2
Figure 5. Degradation behavior of the CoFe
of CoFe /MoS and CoFe in the buffer solution ([1,10-phenanthroline] = 1 g/L, [Catalyst] = 30 mg, pH = 6.86). (b-e) XPS spectra of CoFe
and MoS : (b) Fe 2p, (c) Mo 3d, (d) S 2p, (e) Co 2p. (f) FT-IR spectra of CoFe /MoS , CoFe and MoS . (g) Zeta potential of CoFe /MoS
pH conditions. (h) Schematic diagram of the acidic microenvironment on the CoFe /MoS surface under macroneutral conditions and the mechanism diagram
showing the occurrence of the Fenton-like reaction. (i) Optimized structures of CoFe : Fe-O-Mo bonds on CoFe , Fe-S-Mo bonds on CoFe , and Fe-S-
Mo bonds on CoFe (in an acidic environment).
2
O
4
/MoS
2
-based Fenton reaction system in a neutral buffer solution (pH = 6.86): (a) Fe2+ concentration change curve
/MoS , CoFe
under different
2
O
4
2
2
O
4
2
O
4
2
2 4
O
2
2
O
4
2
2
O
4
2
2
O
4
2
2
O
4
2
2
O
4
2
O
4
2 4
O
2
O
4
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
≡
Fe-S in the Fe 2p XPS spectrum of CoFe
2
O
4
/MoS
2
,[15] which
significantly increases, indicating that the acidity of the catalyst
surface significantly increases.[20] In this case, the enhanced
catalyst surface acidity implies the construction of an acidic
suggests the probable presence of Fe-S-Mo bonds. During the
preparation of the catalyst, thioacetamide has the ability to reduce
≡
Fe3+ on the surface of CoFe
temperature and high pressure. It is worth noting that the chemical
combination with MoS will make the Fe 2p XPS peak position of
CoFe shift to a high binding energy. In addition, the O 1s XPS
2
O
4
to form ≡Fe2+ at high
2 4 2
microenvironment on the CoFe O /MoS surface. In general, an
increase in the surface acidity of the catalyst will make the catalyst
carry a more negative charge, and its point of zero charge (PZC)
value will decrease.[21] However, in our case, with the increase in
2
2
O
4
peak location shifts toward a high binding energy (Figure S24).
Taking into account the essential existence of Fe-O-Co bonds in
2 4 2
the surface acidity of CoFe O /MoS , its surface positive charge
increases, and its PZC value also increases, as shown in Figure
5g. The Zeta potential is the electrical potential at the slipping
plane (ζ-potential) and is not equal to the Stern potential or electric
surface potential in the double layer, as shown in Figure 5h. The
slipping plane is the interface that separates the mobile fluid from
2 4
CoFe O , we consider that the decrease in the electron cloud
density of Fe and O may be due to the introduction of the more
electronegative Mo to form Mo-O-Fe.[16] This conjecture is verified
in the Mo 3d XPS spectra, as shown in Figure 5c. The relative
contents of ≡Mo5+ (228.81 eV, 233.13 eV) and ≡Mo6+ (232.06 eV,
2
the fluid attached to the surface. Taking MoS as an example,
2
35.15 eV) on the surface of MoS
compounding with CoFe
, and the peak location of ≡Mo4+
229.01 eV vs. 228.00 eV, 232.15 eV vs. 231.13 eV) shifts to a
low binding energy. The presence of high-valent Mo indicates that
a redox reaction occurs during the combination of CoFe and
MoS
. Since Fe is less electronegative than Mo,[16] both the Mo-
O-Fe and Mo-S-Fe bonds lead to an increase in the electron cloud
2
significantly increase after
there is a large amount of unsaturated S (one/two-coordination)
+
2
O
4
on the edge of the MoS
2
nanosheets, which will capture H in the
(
solution to form a Stern layer.[8] At this time, the Stern layer
contains a large amount of positive charge, but its potential (Stern
potential) is still negative. Then, as the distance from the particle
surface increases, the positive charge decreases until reaching
the slipping plane. Although there is a positive charge, the
potential is still negative (but the absolute value is reduced), and
2
O
4
2
4
+
density of ≡Mo .
Regarding the S 2p XPS spectrum of MoS
2
in Figure 5d, the
this potential value is the zeta potential. Regarding only MoS
2
or
peaks at 163.24 eV and 162.10 eV reflect S 2p1/2 and S 2p3/2,
respectively[17]. Compared with MoS
, the characteristic XPS
peak strengths of terminal S
2-/S2- (edge S, 164.30 eV)[17-18] and
the polysulfides (terminal S,[19] 161.92 eV) of CoFe
/MoS
significantly increases. This result indicates that the chemical
combination of CoFe mainly occurs at the edge of the MoS
nanosheets, significantly changing the edge S of MoS . This
result is also completely consistent with the previous SEM results
Figure 1d and Figure S2); that is, CoFe particles are mainly
gathered at the edge of MoS . In addition, compared with MoS
most of the S 2p peaks of CoFe /MoS exhibit a remarkable
shift toward a high binding energy, owing to the formation of
Fe(III)-S-Mo or Co(III)-S-Mo between CoFe and MoS . The
Co2p XPS spectra are displayed in Figure 5e, and the content of
Co3+ (781.48 eV and 797. 57 eV) on the surface of CoFe
significantly increases after combining with MoS . During the
hydrothermal preparation of CoFe /MoS , the oxidation ability
of sodium molybdate can promote the formation of Co3+ on the
surface of CoFe , which is also conducive to the formation of
CoFe , their respective surfaces are highly negatively charged
2 4
O
2
in a pH range of 5.0 to 9.0 (Figure 5g). Interestingly, after the
chemical combination of these two catalysts, the negative charge
2
2
O
4
2
2 4 2
on the surface of CoFe O /MoS decreases sharply and even
begins to exhibit a slightly positive charge.
2
O
4
2
2 4
DFT calculations show that, compared with the CoFe O , the
2
bond length of Fe-O increases significantly when there is an Fe-
S-Mo bond or Fe-O-Mo bond on the CoFe surface, and the
2
O
4
(
2
O
4
bond length continues to get longer as the surrounding H+
concentration increases (Figure 5i). That is, in an acidic
microenvironment, the Fe-O bond at the catalyst interface is more
likely to break and generate iron ions, resulting in an increase in
the iron-ion concentration in the Stern layer. Hence, we can infer
that there are many dissolved iron and cobalt ions in the Stern
2
2
,
2
O
4
2
2
O
4
2
≡
2
O
4
2 4 2
layer of CoFe O /MoS (Figure 5h), which makes the zeta
2
potential of the catalyst more positive (Figure 5g). This
mechanism is also a good explanation for the fact that even in a
2
O
4
2
neutral buffer solution, the surface of CoFe
2 4 2
O /MoS still
2
O
4
maintains a stable iron-ion dissolution and iron cycle, while iron
chemical bonds at the interface. Through the above XPS analysis,
we can verify the formation of Mo-O-Fe, Mo-S-Fe and Mo-S-Co
dissolution is not detected in the CoFe
physically mixed system (Figure 5a).
2 4
O system and the
bonds at the interface between CoFe
that there is abundant unsaturated edge sulfur on the surface of
CoFe /MoS , which is conducive to the construction of an
2
O
4
and MoS
2
and confirm
As shown in Figure 5h, the successful construction of an
acidic microenvironment on the surface of CoFe /MoS
2
2
O
4
2
O
4
2
ensures the stable circulation of iron ions on the surface of the
catalyst, which guarantees the subsequent occurrence of a series
acidic microenvironment on the catalyst surface.
To verify the existence of an acidic microenvironment on the
surface, Fourier transform infrared (FT-IR) spectroscopy was
performed on the different catalysts, as shown in Figure 5f. In
of Fenton-like reactions. The cocatalytic effect of MoS
iron circulation on the surface of CoFe /MoS
(Eqs. 1 and 2).[9a]
The ≡Fe2+ on the catalyst surface decomposes H
to generate
2
realizes
2
O
4
2
2
O
2
-1
addition to the peaks of the S-S bonds (821-985 cm ) and Mo-S
•OH. However, due to the short lifetime and limited migration
-
1
bonds (608 cm ), the peak of the CoFe
2
O /MoS
4
2
catalyst at 3200-
distance of •OH, it is easy to continue the reactions to generate
-1
−
and 1
3
400 cm , which is associated with the surface hydroxyl groups,
•O
2
O
2
, as shown in Eqs. 3~6. Moreover, due to the
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
presence of ≡Co3+ and ≡Mo6+ on the surface of CoFe
O
4
/MoS
,
Experimental Details in the Supporting Information.
2
2
−
1
the directional conversion of •O
2
to O
2
is further promoted (Eqs.
~10).[10] Finally, the whole Fenton system is dominated by O
1
to
7
2
Acknowledgements
achieve the efficient degradation of organic pollutants.
To verify the universality of the modification strategy, we
substituted CoFe with Fe and Fe and prepared
Fe /MoS and Fe /MoS catalysts using similar hydrothermal
This work was supported by the State Key Research
Development Program of China (No. 2016YFA0204200). Project
supported by Shanghai Municipal Science and Technology Major
Project (Grant No.2018SHZDZX03) and the Program of
Introducing Talents of Discipline to Universities (B16017).
National Natural Science Foundation of China (Nos. 21822603),
and the Science and Technology Commission of Shanghai
Municipality (20DZ2250400). Authors thank Research Center of
Analysis and Test of East China University of Science and
Technology for the help on the characterization.
2
O
4
2
O
3
3 4
O
2
O
3
2
3
O
4
2
methods. As expected, compared with the single-component
catalysts, all the composite catalysts display a much higher
activity for the degradation of organic pollutants under various
reaction conditions (Figure 2d and S25). Correspondingly, the
composite catalysts maintain a stable iron cycle in the buffer
solution (Figure S26), which ensures the occurrence of the Fenton
reaction. Additionaly, compared with the reported heterogeneous
2 4 2
Fenton systems, the CoFe O /MoS system has significant
advantages in the degradation of organic pollutants (Table S2).
4
+
3+
6+
2+
Author Contributions
≡
Mo + ≡Fe → ≡Mo + ≡Fe
(1)
(2)
6
+
4+
≡
Mo + H O → ≡Mo + H O + O
2
2
2
2
-
‡These authors contributed equally. All authors have given
approval to the final version of the manuscript.
2
+
3+
≡
Fe + H O → •OH + ≡Fe + OH
(3)
(4)
(5)
(6)
2
2
1
4
•OH → O
2
+ 2H O
2
•
2
•
OH + H O → HO + H O
2
2
2
•
2
-
2
+
Conflict of interest
HO → •O + H
2
+
3+
-
2
≡
Fe + O → ≡Fe + •O
(7)
(8)
2
The authors declare no competing financial interest.
2
+
3+
≡
Co + H O → ≡Co + •OH
2
2
-
2
3+
1
2+
•
O + ≡Co → O
2
+ ≡ Co
(9)
Keywords: MoS
2
• heterogeneous Fenton • acidic
-
2
6+
1
4+
•
O + ≡Mo → O
2
+ ≡ Mo
(10)
microenvironment • environmental chemistry • pollutant control
[
1] a) H. J. H. Fenton, J. Chem. Soc., Trans. 1894, 65, 899-910; b) J. Imlay, S. Chin,
S. Linn, Science 1988, 240, 640-642; c) J. Xu, X. Zheng, Z. Feng, Z. Lu, Z. Zhang,
W. Huang, Y. Li, D. Vuckovic, Y. Li, S. Dai, G. Chen, K. Wang, H. Wang, J. K.
Chen, W. Mitch, Y. Cui, Nat. Sustainability 2021, 4, 233-241.
Conclusion
In summary, we successfully constructed an acidic
microenvironment on the surface of CoFe by chemically
bonding with MoS , which ensures the stable circulation of iron
2
O
4
[
[
2] a) B. Shen, C. Dong, J. Ji, M. Xing, J. Zhang, Chin. Chem. Lett. 2019, 30, 2205-
2
2
210; b) X. Yang, X. Cheng, A. A. Elzatahry, J. Chen, A. Alghamdi, Y. Deng,
ions in the slipping plane and overcomes the pH limitation of the
Fenton reaction. Compared with traditional homogeneous and
heterogeneous Fenton technology, the advantages of this
Chin. Chem. Lett. 2019, 30, 324-330.
3] a) H. Jin, X. Tian, Y. Nie, Z. Zhou, C. Yang, Y. Li, L. Lu, Environ. Sci. Technol.
2
017, 51, 12699-12706; b) X. Li, B. Xiao, M. Wu, L. Wang, R. Chen, Y. Wei, H.
CoFe
2 4 2
O /MoS -based Fenton system can be summarized as
Liu, Chemosphere 2020, 245, 125663; c) Z. Ye, J. A. Padilla, E. Xuriguera, J. L.
Beltran, F. Alcaide, E. Brillas, I. Sirés, Environ. Sci. Technol. 2020, 54, 4664-4674;
d) K. Chen, G.-H. Wang, W.-B. Li, D. Wan, Q. Hu, L.-L. Lu, Chin. Chem. Lett.
2014, 25, 1455-1460.
follows: a) the acidic microenvironment on the surface realizes the
3
+
2+
stable circulation of ≡Fe /≡Fe on the catalyst surface in neutral
or weakly alkaline solutions; b) this system can truly overcome the
pH limitation and realize the long-term degradation of organic
pollutants, such as phenol, in neutral buffer solutions; c) the
generation of iron sludge under neutral conditions is significantly
reduced, and the comprehensive operating cost of Fenton
technology is decreased; and d) the preparation and operation of
[4] J. L. Buitrago, J. Sanabria, H. M. Gútierrez-Zapata, F. J. Urbano-Ceron, A. García-
Barco, P. Osorio-Vargas, J. A. Rengifo-Herrera, Environ. Sci. Pollut. Res. 2020,
27, 1608-1624.
[5] a) K. Toda, T. Tanaka, Y. Tsuda, M. Ban, E. P. Koveke, M. Koinuma, S.-I. Ohira,
J. Hazard. Mater. 2014, 278, 426-432; b) Q. Ouyang, F. Kou, P. E. Tsang, J. Lian,
J. Xian, J. Fang, Z. Fang, J. Cleaner Prod. 2019, 232, 1492-1498.
[6] C. P. Veeramalai, F. Li, Y. Liu, Z. Xu, T. Guo, T. W. Kim, Appl. Surf. Sci. 2016,
389, 1017-1022.
the MoS
2
cocatalytic modification strategy is simple and easy. The
/MoS aims at the advanced
successful application of CoFe
2
O
4
2
treatment of actual industrial wastewater, and the elimination of
dye wastewater in pilot devices under neutral conditions provides
theoretical and feasible results for the practical application of
[7] a) B. Qiu, Y. Deng, M. Du, M. Xing, J. Zhang, Sci. Rep. 2016, 6, 1-10; b) J. Dai,
W. Feng, C. Cheng, X. Wen, Mater. Res. Express 2020, 7, 045009; c) F. D.
Saccone, S. Ferrari, D. Errandonea, F. Grinblat, V. Bilovol, S. Agouram, J. Appl.
Phys. 2015, 118, 075903.
2
MoS -mediated heterogeneous Fenton reactions.
Experimental Section
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
[
8] K. Chang, Z. Mei, T. Wang, Q. Kang, S. Ouyang, J. Ye, ACS Nano 2014, 8, 7078-
087.
9] a) M. Xing, W. Xu, C. Dong, Y. Bai, J. Zeng, Y. Zhou, J. Zhang, Y. Yin, Chem
018, 4, 1359-1372; b) L. Zhu, J. Ji, J. Liu, S. Mine, M. Matsuoka, J. Zhang, M.
7
[
2
Xing, Angew. Chem. Int. Ed. 2020, 59, 13968-13976; c) J. Liu, C. Dong, Y. Deng,
J. Ji, S. Bao, C. Chen, B. Shen, J. Zhang, M. Xing, Water Res. 2018, 145, 312-320.
10] a) Q. Yi, J. Ji, B. Shen, C. Dong, J. Liu, J. Zhang, M. Xing, Environ. Sci. Technol.
[
2
019, 53, 9725-9733; b) J. Ji, Q. Yan, P. Yin, S. Mine, M. Matsuoka, M. Xing,
Angew. Chem. Int. Ed. 2021, 60, 2903-2908.
[
[
11] J. Ji, R. M. Aleisa, H. Duan, J. Zhang, Y. Yin, M. Xing, iScience 2020, 100861.
12] a) O. Pestovsky, S. Stoian, E. L. Bominaar, X. Shan, E. Munck, L. Que, Jr., A.
Bakac, Angew. Chem. Int. Ed. 2005, 44, 6871-6874; b) J. Park, Y. Morimoto, Y.
M. Lee, W. Nam, S. Fukuzumi, J. Am. Chem. Soc. 2011, 133, 5236-5239; c) A.
Ansari, A. Kaushik, G. Rajaraman, J. Am. Chem. Soc. 2013, 135, 4235-4249.
13] S. Pang, J. Jiang, J. Ma, Environ. Sci. Technol. 2011, 45, 307-312.
[
[
14] a) Z. Wang, J. Jiang, S. Pang, Y. Zhou, C. Guan, Y. Gao, J. Li, Y. Yang, W. Qiu,
C. Jiang, Environ. Sci. Technol. 2018, 52, 11276-11284; b) Y. Gao, Y. Zhou, S.-
Y. Pang, Z. Wang, Y.-M. Shen, J. Jiang, Chem. Eng. J. 2020, 387, 124077; c) Z.
Wang, W. Qiu, S. Pang, Y. Gao, Y. Zhou, Y. Cao, J. Jiang, Water Res. 2020, 172,
1
15504.
[
15] M. V. Morales-Gallardo, A. M. Ayala, M. Pal, M. A. Cortes Jacome, J. A. Toledo
Antonio, N. R. Mathews, Chem. Phys. Lett. 2016, 660, 93-98.
[
[
[
16] K. Li, D. Xue, J. Phys. Chem. A 2006, 110, 11332-11337.
17] N. Xue, P. Diao, J. Phys. Chem. C 2017, 121, 14413-14425.
18] C. Backes, R. J. Smith, N. McEvoy, N. C. Berner, D. McCloskey, H. C. Nerl, A.
O’Neill, P. J. King, T. Higgins, D. Hanlon, N. Scheuschner, J. Maultzsch, L.
Houben, G. S. Duesberg, J. F. Donegan, V. Nicolosi, J. N. Coleman, Nat. Commun.
2
014, 5, 4576.
19] M. Fantauzzi, B. Elsener, D. Atzei, A. Rigoldi, A. Rossi, RSC Adv. 2015, 5, 75953-
5963.
20] M. Xia, M. Long, Y. Yang, C. Chen, W. Cai, B. Zhou, Appl. Catal. B: Environ.
011, 110, 118-125.
[
[
[
7
2
21] C. Moreno-Castilla, M. A. Ferro-Garcia, J. P. Joly, I. Bautista-Toledo, F. Carrasco-
Marin, J. Rivera-Utrilla, Langmuir 1995, 11, 4386-4392.
This article is protected by copyright. All rights reserved.

Angewandte Chemie International Edition
10.1002/anie.202105736
RESEARCH ARTICLE
Entry for the Table of Contents (Please choose one layout)
Layout 1:
RESEARCH ARTICLE
‡
‡
We have successfully constructed an
acidic microenvironment on the
Qingyun Yan , Cheng Lian , Kai Huang,
Lihong Liang, Haoran Yu, Pengcheng
Yin, Jinlong Zhang, and Mingyang Xing*
surface of CoFe
2
O
4
by chemical
bonding MoS which ensures the
2
,
stable circulation of iron ions in the
slipping plane and truly overcomes the
limitation of pH in pollutant control,
thereby expanding the applicability of
Fenton technology.
Page No. – Page No.
Constructing an Acidic
Microenvironment by MoS in
2
Heterogeneous Fenton Reaction for
Pollutant Control
This article is protected by copyright. All rights reserved.