Parisa Paydara and Ali Faghihi Zarandi a,*
a Occupational Health Engineering Department, School of Public Health, Kerman University of Medical Sciences, Kerman, Iran
Research Article, Issue 1
Analytical Methods in Environmental Chemistry Journal
Journal home page: www.amecj.com/ir
AMECJ
------------------------
substances, heavy metals are essentially non-
biodegradable and therefore accumulate in the
environment. This contamination poses a risk to
environmental and human health. Some heavy
metals are carcinogenic, mutagenic, teratogenic
and endocrine disruptors while others cause
neurological and behavioral changes especially
in children. Thus remediation of heavy metal
pollution deserves due attention. Different physical
and chemical methods used for this purpose. Heavy
metals enter the environment from natural and
anthropogenic sources [1]. The most significant
natural sources are weathering of minerals,
erosion and volcanic activity while anthropogenic
Air Pollution Method: A new method based on ionic liquid
passed on mesoporous silica nanoparticles for removal of
manganese dust in the workplace air
1. Introduction
Environmental pollution by heavy metals has
become a serious problem in the world. The
mobilization of heavy metals by man through
extraction from ores and processing for different
applications has led to the release of these elements
into the environment. The problem of heavy metals’
pollution is becoming more and more serious with
increasing industrialization and disturbance of
natural biogeochemical cycles. Unlike organic
* Corresponding Author: Ali Faghihi Zarandi
Email: alifaghihi60@yahoo.com
https://doi.org/10.24200/amecj.v2.i01.52
Removal of manganese dust from workplace air; Parisa Paydar & et al
A R T I C L E I N F O:
Received 15 Dec 2018
Revised form 22 Jan 2019
Accepted 9 Feb 2019
Available online 17 Mar 2019
Keywords:
Manganese dust
Air pollution
Ionic liquid
Mesoporous silica nanoparticles
Solid phase adsorption method
A B S T R A C T
Chronic effect of manganese exposure to humans caused the dysfunction
of nervous system. An applied sorbent based on hydrophobic ionic
liquid passed on mesoporous silica nanoparticles (IL/MSNPs) was
used for adsorption/removal of manganese dust (Mn) from workplace
air by solid phase adsorption method (SPAM). In bench scale set up, 5
mL of standard solution of nitrate and oxide of Mn (0.2-5 mg L-1) was
used for generation of manganese dust in pure air by drying procedure,
and then was passed through column of IL/MSNPs by SKC pump with
flow rate of 200-500 mL min-1 by SKC pump. Moreover, Mn particles
were become absorbed/removal from artificial air by IL/ MSNPs at
80 oC. The Mn particles separated from column of IL/MSNPs by
irrigation of nitric acid solution (2 mL of 0.3 M) before determined by
F-AAS/ET-AAS. In optimized conditions, the adsorption capacity of
MSNPs and IL/MSNPs for Mn removal from air in batch system (1 Li)
was obtained 118.5 mg g-1 and 216.2 mg g-1 respectively. Ultimately,
for validation, spike of Mn particles (bag 1 Li) and ICP was used for
dynamic system.
Analytical Methods in Environmental Chemistry Journal Vol 2 (2019) 5-14
6Analytical Methods in Environmental Chemistry Journal; Vol. 2 (2019)
sources include mining, smelting, electroplating,
use of pesticides, and (phosphate) fertilizers as
well as bio-solids in agriculture, sludge dumping,
industrial discharge, atmospheric deposition etc.
[2]. Examples of essential heavy metals are Fe, Mn,
Cu, Zn, and Ni [3,4]. Non-essential heavy metals
are those, which are not needed by living organisms
for any physiological and biochemical functions.
Examples of nonessential heavy metals are Cd,
Pb, As, Hg, and Cr [5,6]. Blood, urine, and hair are
the most accessible tissues in which to measure an
exposure or dose; they are sometimes referred to
as indicator tissues. Blood and urine concentrations
usually reflect recent exposure and correlate best
with acute effects. In addition, air might be useful
in assessing variations in exposure to metals over
the long term. Manganese is one of the essential
metals for the body. Also, this metal (Mn) is a
required element and a metabolic byproduct of the
contrast agent mangafodipirtrisodium (MnDPDP)
[7]. In addition, exposure to manganese in the
workplace is an occupational health concern, it is
known that even at relatively low levels of exposure
subtle neurological effects have been observed
in workers [8]. Manganese is a transitional metal
and can exist in 11 oxidation states, from 3- to 7+.
The most common valences are 2+, 4+, and 7+. The
most common valence in biological systems is 2+;
moreover, the valence of 4+ is present as MnO2.
Mn+3 is also important in biological systems.
Cycling between Mn+2 and Mn+3 may be potentially
deleterious to biological systems because it can
involve the generation of free radicals. Manganese
is an essential element and is a cofactor for a
number of enzymatic reactions, particularly those
involved in phosphorylation, cholesterol, and fatty
acids synthesis. Manganese is present in all living
organisms [9,10]. The industrial use of manganese
has also expanded in recent years as a ferroalloy
in the iron industry and as a component of alloys
used in welding [11]. Manganese welding is one
of the industries exposed to high concentrations
of manganese. In this process, manganese metal
fumes are produced. According to the NIOSH
standard, the exposure limit for this metal is 0.2 mg
m-3 [12]. The most common form of manganese
toxicity is the result of chronic inhalation of
airborne manganese in mines, steel mills, and
some chemical industries [10]. Industrial toxicity
from inhalation exposure, generally to manganese
dioxide in mining or manufacturing, is of two
types: The first, manganese pneumonitis, is the
result of acute exposure. Men working in plants
with high concentrations of manganese dust show
an incidence of respiratory disease 30 times greater
than normal. Pathologic changes include epithelial
necrosis followed by mononuclear proliferation.
Mn toxicity has been reported through occupational
(e.g. welder) and dietary overexposure and is
evidenced primarily in the central nervous system,
although lung, cardiac, liver, reproductive, and
fetal toxicity have been noted. Mn neurotoxicity
results from an accumulation of the metal in
brain tissue and results in a progressive disorder
of the extrapyramidal system which is similar to
Parkinson’s disease. In order for Mn to distribute
from blood into brain tissue, it must cross either
the blood–brain barrier (BBB) or the blood–
cerebrospinal fluid barrier (BCB). Brain import,
with no evidence of export, would lead to brain
Mn accumulation and neurotoxicity [13,14]. At the
present time, the most commonly used methods
for assessing workplace airborne metal exposures
involve collecting air samples on filters and sending
them to a fixed-site laboratory where a variety of
analytical methods are used. The National Institute
for Occupational Safety and Health (NIOSH) has
developed one quantitative field-portable methods
to measure airborne lead: NIOSH Method 7300,
which uses inductively coupled argon plasma,
atomic emission spectroscopy (ICP-AES) [15,
16]. Also, many analytical techniques have been
employed for the determination of trace levels of
lead in real samples such as, high performance liquid
chromatography coupled to inductively coupled
plasma mass spectrometry (HPLC-ICP-MS)[17],
Inductively coupled plasma mass spectrometry
(ICP-MS)[18], inductively coupled plasma atomic
emission spectrometry (ICP-AES)[19], flame
atomic absorption spectrometry (F-AAS) [20],
7
Removal of manganese dust from workplace air; Parisa Paydar & et al
electrothermal atomic absorption spectrometry
(ET-AAS)[21], etc. Nowadays, considerable
novel method has been introduced in solid-phase
extraction (SPE) by applying new nanomaterials
with remarkable physicochemical properties
that improve the extraction of analytes. Thus,
many carbonaceous materials such as activated
carbons[22], carbon nanotubes[23], carbon
nanohorns [24], carbon nanocones/disks [25] and
graphene [26- 28] have been applied for analytical
preconcentration due to their unique properties,
such as reduced particle size, big surface area, high
adsorption capacity and good chemical stability
[29]. Porous solids are used technically as adsorbents
catalysts and catalyst supports owing to their high
surface areas. According to the IUPAC definition
[30]. Larger pores are present in porous glasses
and porous gels which were known as mesoporous
materials at the time of the discovery of MCM-
41. With MCM (Mobil Composition of Matter)
41 the first mesoporous solid was synthesized
that showed a regularly ordered pore arrangement
and a very narrow pore-size distribution. After the
discovery of MCM-41 in 1992. This material has
a highly ordered mesoporous hexagonal structure
with mesopore diameters varying from 5 to 30 nm
porous materials are divided into three classes:
pore-size distributions. Other mesoporous solids
microporous (<2 nm), mesoporous (2-50 nm)
and were synthesized via intercalation of layered
mate macroporous (>50 nm). The pore size and
the thickness of the silica walls can be adjusted
by varying the heating temperature and time in
the reaction solution [31]. Careful investigation
of structure of SBA-15 showed that material has
certain amount of micropores which connect
neighboring mesopores [32,33]. The threshold
limit values, permissible exposure limit and
occupational exposure limits (TLV/ PEL/OEL) of
manganese particles exposure in air determined by
international organizations such as, occupational
safety and health administration (OSHA, PEL),
national institute of occupational safety and health
(NIOSH, OEL) and American conference of
governmental industrial hygienists (ACGIH, TLV)
and were 5mg m-3, 3mg m-3, 5mg m-3 respectively
[34].
So, adsorption/ removal of manganese particles
from work place air has more important, due to
the high toxicity in human body. In this study, IL/
MSNPs and MSNPs were used for adsorption/
removal of manganese dust (Mn) from workplace
air by SPAM. The flow rate, mass / type of sorbent,
temperature, and length column are important
parameters which have more effected on removal
efficiency of MSNPs from workplace and artificial
air. The mean of relative standard deviation and
preconcentration factor was less than 5% and 2.5,
respectively.
2. Experimental procedure
2.1. Reagents and instrumental
Determination of manganese was performed with
a spectra GBC flame or electro-thermal atomic
absorption spectrometer (Model, Plus 932, Aus).
A Mn hollow cathode lamp operating at a current
of 5 mA and a wavelength of 279.5 nm with a
spectral bandwidth of 0.2 nm was used. The GBC
demountable torch of inductively coupled plasma
optical emission spectrometer (ICP-OES, Integra
XL, GBC, Aus) with efficient and high performance
at reduced gas flow was used for manganese
determination. The innovative bayonet mount torch
design requires absolutely no re-alignment when
replacing individual components. The Integra’s
standard set of sample introduction components
offer unique capabilities that overcome traditional
limitations. Optical detector based on dual
photomultiplier system (R7154 solar blind tube)
with UV detection was used. The plasma gas with
10 L min-1 (Ar), auxiliary gas with 0.5 L min-1 (Ar),
and nebulizer gas with 0.5 L min-1 (Ar) were used.
The instrumental conditions are shown in Table 1.
All reagents with analytical grade were purchased
from Merck/Sigma (Darmstadt, Germany). Mn
(II) and Mn (V) were prepared by dissolving
appropriate amounts of Mn (NO3)2, MnO, and
KMnO4 in DW. The experimental and working
standard solutions were prepared daily by diluting
the stock solutions with DW. Deionized water
8Analytical Methods in Environmental Chemistry Journal; Vol. 2 (2019)
prepared and simulated in beach scale set up by
standard solution of Mn (Fig. 1). The Mn nitrate
and oxide was generated from 5 mL of standard
solution (0.1 – 5 mg L-1) after drying up to 110
oC by which was mixed with pure air (210 mL of
O2/L; 2.5 mL of H2O /L) at 25 oC. This mixture was
moved to column which was filled with 20 mg of
IL/MSNPs, MSNPs and IL by flow rate of 450 mL
min-1. After adsorption Mn dusts on sorbent, the
column irrigated with 2 mL of nitric acid (0.3 M) and
concentration of Mn in final solution determined
by F-AAS and ICP-OES. Note, the IL paste on
MSNPs caused to increase the adsorption capacity
of Mn dust from air as compared to MSNPs. By
oC, the removal
efficiency was almost increased. The removal
efficiency of proposed method was calculated by
ratio of concentration of Mn in bulk of pilot to
concentration of Mn which was determined by
ICP-OES/F-AAS. For validation of methodology,
different concentration of Mn was generated by
pilot and spike to air samples dust. The recovery
and adsorption capacity (mg g) was calculated
at 50oC as follows: Cs and Cb ( mL-1 or mg L-1)
are concentration in sample and blank solution
respectively. Ci and Cf are the initial and final
concentrations of MnO/Mn(NO3)2. In addition, the
V( mL) and m(mg) were the volume solution and
mass of sorbent, respectively. The recovery was
calculated by using Equation 2.
Eq. 1 Adsorption capacity (mg g) = [(Ci−Cf) V] /m
Eq. 2 Recovey%
100%covRe ×
−
=
Ci
)C(C
ery fi
2.4. Characterizations
X-ray diffraction (XRD) patterns were reported
radiation (1.54 Å ) operating at 36.5 kV and 30
mA. Diffraction data was recorded between 1 and
-1. Scanning electron micrograph
was recorded using a Zeiss DSM 962 (Zeiss,
Oberkochen, Germany). The sample was deposited
prepared by water purification system (Millipore,
Bedford, MA, USA). Cetylmethyl NH4Br (CTAB),
Na2SiO2 (28 wt % SiO2, 8 wt % Na2O, 64 wt %
H2O), silica gel, C2H5OH, NaOH, HCl and HNO3
all were purchased from Merck, Germany. All
chemicals such as HNO3 and NaOH, acetone were
used as purchased and no further purification was
performed.
2.2. Synthesis
For synthesis, 3.13 grams of CTAB was added to
70.6 g of DW and stirred to change clear. First, 7.8
g of ethanol was added to the surfactant solution
and then, 9.7 g of sodium silicate (28 wt.% SiO2, 5
wt.% Na2O, 65 wt.% H2O) was mixed to surfactant
solution (white suspension). Second, 24.6 g of
sodium carboxyl methyl cellulose solution (12
wt.%) was added to the suspension and stirred for 3
h followed by 2 days aging in oven at 70 oC. Then,
the precipitate of MSNPS was filtered, washed with
deionized water and dried at 100oC overnight. The
MSNPS was placed in a furnace and calcined with
a heating rate of 1 K min-1 to 550oC and held at this
temperature for 6 hours in air. Then, hydrophobic
ionic liquid (HIL) of 1-butyl-3-methylimidazolium
hexafluorophosphate ([BMIM][PF6]) passed on
mesoporous silica nanoparticles (IL/MSNPs). In
addition, 0.4 g of the [BMIM][PF6] with 3 mL
of acetone mixed with 20 mg of MSNPS and after
shaking for 3 min, drying up to 75 oC. MSNPS
modified with IL was made for further study.
2.3. Procedure
The dust of Mn nitrate and oxide in pure air was
Table 1. Instrumental Conditions for Mn determination
by ICP-OES and F-AAS.
ICP-OES F-AAS
Element Mn Mn
Wavelength (nm) 279.48 279.5
Lamp current (mA) -- 5.0
Slit (nm) --- 0.2
Volume spray injection 0.2 per min 2 mL
LOD (µg mL-1) 0.1 0.33
Range a (µg mL-1)0.5-10
Mode Peak area Peak area
9
Removal of manganese dust from workplace air; Parisa Paydar & et al
on a sample holder with an adhesive carbon foil
and sputtered with gold. Adsorption/desorption
of Nitrogen was carried out at 77 K using a
BELSORP-mini porosimeter. Prior to analysis the
samples were outgassed in-vacuo for 5 hours at 280
°C until a stable vacuum of 0.12 Pa was reached.
The pore size distribution was calculated from
the desorption branches of isotherms using the
standard BJH procedure and also with geometrical
(pressure independent) method. Transmission
electron microscopy (TEM) was performed on a
LEO Zeiss 912 AB. The morphology of MSNPs
was examined using scanning electron microscopy
(SEM) by Phillips, PW3710, Netherland Company.
Sample were dispersed in ethanol and sonicated
for 30 minutes and deposited on a copper grid. The
synthesis was prepared as the weight of calcined
solid per grams of SiO2 in the initial mixture. The
elemental analyzer (CHNS/O, PerkinElmer, 2400
Series II) was used for determination of elemental
composition of samples. CHN instrument perform
elemental ratio calculations of H/C, N/C, S/C or
C/N.
3. Results and discussion
3.1. SEM and TEM imaging
As shown in Figure 2, IL/MSNPs have a highly
porous morphology and the mesoporous silica
particles are in nanometer range (40-60 nm).
Moreover, IL passed on MSNPs did not led to bulky
silica nanoparticles. TEM image also illustrates
pore structure of IL/MSNPs was shown in figure 5.
Based on TEM, the mesoporous are clearly visible
in the silica nanoparticles and particle size of the
samples is in nanometer range as those observed in
SEM image.
Fig. 1. Beach scale set up with standard solution of Mn by SPAM.
Fig. 2. TEM and SEM of IL/MSNPs sorbent
TEM
10 Analytical Methods in Environmental Chemistry Journal; Vol. 2 (2019)
3.2. Effect of the Mass of MSNPs/IL
The removal efficiency of Mn particles from air
with IL/MSNPs was examined between 5-50 mg.
The results showed, 15 mg of sorbent had more
efficiency for Mn dust removal from air (more than
95%). So, 20 mg of IL/MSNPs was selected as
the optimum amounts of adsorbent in gas phase by
proposed method. Based on results, 20 mg [BMIM]
[PF6] and [EMIM][PF6] and [HMIM][PF6] can be
removal Mn dust from air up to 38.4%, 26%, and
32%, respectively. So, [BMIM][PF6] was used as
IL in this research.
3.3. Removal efciency and Adsorption capacity
In this study, the parameters effected on removal
efficiency and adsorption capacity were studied
OC), flow rates
(50, 100, 200,400 and 600 mL min-1) and initial
concentrations of 0.1-5 mg L-1 (ppm). Finally, the
adsorption capacity of 216.2 mg g-1, 118.5 mg g-1
and 67.4 mg g-1 was obtained for Mn dust removal
from air with 20 mg IL/MSNPs, MSNPs and IL,
respectively. Different ILs such as [BMIM][PF6]
and [EMIM][ PF6] and [HMIM][PF6] passed on
MSNPs and effect of temperature on Mn adsorption
process was investigated. The results showed,
increasing of temperature between 38-70 oC,
decreased the viscosity of ILs and caused to efficient
removal of Mn dust from air, so, 50oC was selected
as optimum temperature. Initial concentrations of
0.01-1 mg L-1 (ppm) of Mn dust were examined
by proposed procedure. It seems that, the initial
concentrations of Mn dusts depended on mass
of sorbent/IL and adsorption capacity. When the
adsorption capacity of IL/MSNPs was increased,
the more concentration of Mn can be used. As a 20
mg of sorbent and adsorption capacity of 216 mg
g-1, the maximum concentration of 4.32 mg of Mn
was obtained.
3.4. Effect of air ow rate
By SPAM procedure, the effect of flow rate for Mn
dust removal from air was studied for 30 samples.
The effect of different flow rates for 20 mg IL/
MSNPs, MSNPs, and IL between 50 to 800 mL
min-1 was tested at room temperature and 50oC. The
flow rate was measured in output of solid phase by
a rotameter. The removal efficiency and adsorption
capacity of IL/MSNPs, MSNPs and IL for Mn dust
were obtained less than 500 mL min-1. So, 450 mL
min-1 was selected as optimum flow rate with IL/
MSNPs phase for removal of Mn dust from air
(Fig. 4).
3.5. Method Validation and Column Condition
The back extraction of Mn from IL/MSNPs was
occurred with the minimal concentration of different
acid solution. By SPAM method, the different acid
solution was used for back extraction Mn ions from
column. Reducing pH, leads to dissociation and
Fig. 2. The effect of concentration for manganese removal from air.
11
Removal of manganese dust from workplace air; Parisa Paydar & et al
releasing of Mn (II) ions from IL/MSNPs, MSNPs
and IL into acid phase. In order to determine the
type and amount of mineral acidic solution for lead
desorption from IL/MSNPs, different mineral acids
such as HCl, HNO3 and H2SO4 (0.1-1 mol L-1) were
studied by proposed procedure. The results showed,
the 0.3 mol L-1 of HNO3 solution was selected as a
quantitatively acid solution for back extraction of
Mn(II) from IL/MSNPs. By experimental design,
the interaction between manganese dust in air
and IL/MSNPs as a sorbent was evaluated when
the pilot set up correctly. In this method, the IL/
MSNPs, MSNPs and IL was used for removal of
for Mn dust (MnO and Mn(NO3)2) from air by
SPAM. For calculating of accuracy and precision
of dynamic system, the initial Mn concentration in
bench scale set up (bulk container) was determined
by F-AAS and compared to proposed method by
sorbents. By proposed method, the Mn dust with
different concentration from 0.1-1 mg L-1 was
generated and passed through dynamic system
with 450 mL min-1 and removal from air by 20
Fig. 4. Effect of flow rate on recovery percentage.
Fig. 3. The effect of temperature for manganese removal from air.
12 Analytical Methods in Environmental Chemistry Journal; Vol. 2 (2019)
mg of IL/MSNPs. The different concentration of
standard of MnO and Mn(NO3)2 in air bags and
bulk container was determined by F-AAS before
used by proposed method. Since standard reference
material (SRM) for Mn nitrate and oxide in air
dust are not currently available, the spiked of Mn
concentration in air which was generated by bench
-1, 450 mL min-1) were prepared
to demonstrate the reliability of the method by
IL/MSNPs, MSNPs and IL sorbents (Table 2, 3).
For determination of manganese concentration
in lower and upper linear range, the sample was
preconcentration and dilution up to 2.5 and 12.5,
respectively. At optimized set up, more than 98%
of Mn oxide and nitrate in air dust were removed
by IL/MSNPs at 50oC. The high recovery of
spiked samples is satisfactorily reasonable and was
confirmed using addition method, which indicates
the capability of SPAM method for removal of Mn
dust from air. After irrigation of column with 2
mL of nitric acid (0.3 M, pH<4), the Mn ions was
back extracted from IL/MSNPs as a solid phase
and Mn concentration determined by F-AAS. The
validation of methodology was confirmed using
power instrumental analyzer ICP (Table 4).
4. Conclusions
In this research, the adsorption/removal of pollutant
Mn dust from air was achieved based on IL/MSNPs
and MSNPs by SPAM. The results showed, the
unique, efficient, and applied procedure which
was used for removal of Mn particles dust from
workplace and artificial air. For increasing of
removal recovery, Mn concentration, amount of
IL/MSNPs, temperature from 20-100 and flow
rate were studied and optimized. The capacity
adsorption, recovery, removal efficiency of sorbents
was investigated and compared together by F-AAS
and ICP-OES. Based on the results, the adsorption
capacity IL/MSNPs were more than MSNPs for
nitrate/oxide of Mn dust from workplace air. In
addition, the efficiency of adsorption for MnO
Table 2. Method validation for IL/MSNPs by spike of Mn oxide in dust air with F-AAS (mg L-1)
Bench
(Conc.)
Bulk Bench
(Conc.)
Added to bench
(Conc.)
FoundaRecovery (%)
b0.2 0. 16 ± 0.02 0.2 0..31 ± 0.03 96.8
b0.3 0.28 ± 0.02 0.3 0.53 ± 0.05 94.6
b0.5 0.44 ± 0.04 0.5 0.87 ± 0.07 98.9
1.0 0.95 ± 0.08 1.0 1.85 ± 0.11 97.3
c3.0 2.78 ± 0.16 3.0 5.62 ± 0.27 101.2
c5.0 4.69 ± 24 5.0 9.02± 48 96.1
a Mean of three determinations ± confidence interval (P = 0.95, n = 5)
b (Preconcentration Factor=2.5, Injection volume=2 mL, 450 mL min-1 air flow rate, Peak Area, 20 mg, T=50oC, pH<4)
c (Dilution Factor=2.5, Injection volume=12.5 mL, 450 mL min-1 air flow rate, Peak Area, 20 mg, T=50oC, pH<4)
Table 3. Method validation for IL/MSNPs by spike of Mn nitrate in dust air with F-AAS (mg L-1)
Bench
(Conc.)
Bulk Bench
(Conc.)
Added to bench
(Conc.)
FoundaRecovery (%)
b0.4 0. 35 ± 0.02 0.4 0..67 ± 0.04 95.7
b0.6 0.52 ± 0.05 0.6 0.99 ± 0.10 95.2
1.0 0.92 ± 0.09 1.0 1.88 ± 0.12 102.3
2.0 1.86 ± 0.13 2.0 3.65 ± 0.18 98.1
c3.0 2.65 ± 0.17 3.0 5.18 ± 0.28 97.7
c5.0 4.51 ± 0.25 5.0 8.94± 0.48 99.1
a Mean of three determinations ± confidence interval (P = 0.95, n = 5)
b (Preconcentration Factor=2.5, Injection volume=2 mL, 450 mL min-1 air flow rate, Peak Area, 20 mg, T=50oC, pH<4)
c (Dilution Factor=2.5, Injection volume=12.5 mL, 450 mL min-1 air flow rate, Peak Area, 20 mg, T=50oC, pH<4)
13
Removal of manganese dust from workplace air; Parisa Paydar & et al
and Mn (NO3)2 was increased at more than 38-70
OC and decreased more than 90 oC. Finally, the
results showed that the flow rate is important factor
in dynamic system, and optimized flow rate was
achieved less than 450 mL min-1. The method had
good ability for removal of Mn dust from air.
5. Acknowledgments
We are thankful to Research Institute of Petroleum
Industry (RIPI) and Iranian Petroleum Industry
Health Research Institute (IPIHRI).
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Table 4. Comparing of different sorbents for removal of Mn oxide by ICP-OES/F-AAS (mg L-1)
Sample* Bulk Bench
(Conc.)
Added
(Conc.)
F-AAS a
(Conc.)
ICP-OES a
(Conc.)
FAAS
Recovery (%)
ICP-OES
Recovery (%)
IL 1.0 ----- 0.26± 0.02 0.29± 0.02 26 29
1.0 0.54± 0.03 0.56± 0.04 28 27
2.0 0.83± 0.04 0.88± 0.05 28.5 29.5
IL/MSNPs 1.0 ----- 0.98± 0.05 0.99± 0.06 98 99
1.0 1.99± 0.09 1.97± 0.10 101 98
2.0 2.96± 0.15 2.95± 0.16 99 98
MSNPs 1.0 ----- 0.52± 0.03 0.56± 0.02 52 56
1.0 1.03± 0.05 1.11± 0.06 51 55
2.0 1.49± 0.07 1.64± 0.08 48.5 54
a Mean of three determinations ± confidence interval (P = 0.95, n = 5)
* (450 mL min-1 air flow rate, Peak Area, 20 mg, T=50oC, pH<4)
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