# The Research of Nanoparticle and Microparticle Hydroxyapatite Amendment in Multiple Heavy Metals Contaminated Soil Remediation

Authors: Zhangwei Li; Man-man Zhou; Weidian Lin
Journal: Journal of Nanomaterials
 (2014)

---

## Abstract

It was believed that when hydroxyapatite (HAP) was used to remediate heavy metal-contaminated soils, its effectiveness seemed likely to be affected by its particle size. In this study, a pot trial was conducted to evaluate the efficiency of two particle sizes of HAP: nanometer particle size of HAP (nHAP) and micrometer particle size of HAP (mHAP) induced metal immobilization in soils. Both mHAP and nHAP were assessed for their ability to reduce lead (Pb), zinc (Zn), copper (Cu), and chromium (Cr) bioavailability in an artificially metal-contaminated soil. The pakchoi (Brassica chinensis L.) uptake and soil sequential extraction method were used to determine the immobilization and bioavailability of Pb, Zn, Cu, and Cr. The results indicated that both mHAP and nHAP had significant effect on reducing the uptake of Pb, Zn, Cu, and Cr by pakchoi. Furthermore, both mHAP and nHAP were efficient in covering Pb, Zn, Cu, and Cr from nonresidual into residual forms. However, mHAP was superior to nHAP in immobilization of Pb, Zn, Cu, and Cr in metal-contaminated soil and reducing the Pb, Zn, Cu, and Cr utilized by pakchoi. The results suggested that mHAP had the better effect on remediation multiple metal-contaminated soils than nHAP and was more suitable for applying in in situ remediation technology.


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## Body

## 1. Introduction

Heavy metal pollution in the soil has become a serious environmental problem in China, particularly following the rapid industrialization of the nation. Heavy metal in soil readily accumulates in plants and is then transported through the food chain, thus becoming a major threat to human health [1]. A number of remediation methods have been developed in an attempt to control heavy metal pollution, including the use of organic manure, soil amendment addition, cultivation of heavy metal hyperaccumulator plants, and the application of agroecological engineering techniques [2, 3].Supplementation of phosphate-based materials has been found to have a great effect on immobilizing Pb in contaminated soil and has recently become a commonly used technique due to its cost-effectiveness and decreased disruptive nature [4, 5]. Hydroxyapatite (HAP) is considered to be the most effective supplement among P-based materials and is commonly used in Pb-contaminated soil. It has been reported that HAP not only facilitates the remediation of Pb, but it is also quite effective in immobilizing other heavy metals, such as Zn, Cd, and Cu [6, 7]. However, the overall effectiveness of using phosphate to immobilize metals and its mechanisms of action remain unknown.With the rapid development of nanotechnology there has been an increased usage of HAP nanoparticles put into use in wastewater and for soil remediation. Nanometer size particle HAP (nHAP) has a larger specific surface area than micrometer sized particle HAP (mHAP). Moreover, theoretically nHAP has larger reactivity and sorption capacities than that of common size of HAP [8, 9]. However, few studies have focused on the remediation differences between mHAP and nHAP. Furthermore, little work has been done identifying the effectiveness of the effect of nHAP on a number of different heavy metals. Therefore, the aim of this study was to compare the effectiveness/differences between mHAP and nHAP to reduce the uptake of multiple heavy metals (Pb and Zn, Cu and Cr) by plants and to immobilize these heavy metals in contaminated soil.


## 2. Material and Methods

### 2.1. Soil Sample Properties

The soil samples were derived from vegetable gardens. After being air-dried, the soil samples were grounded to pass through a 10 mm sieve for the pot trial. Soil pH was measured in 1 : 2.5 soil water suspensions with a combination pH electrode. Soil organic matter was determined by wet digestion with K2Cr2O7 and H2SO4; available N, P, and K were determined according to standard methods recommended by Lu [10]. Some basic physiochemical properties of the soil and the concentrations of Pb, Zn, Cu, and Cr in this soil were listed in Table 1.Table 1
Basic properties of the soil.
pH
Organic matter (g·kg−1)
Available (mg·kg−1)
Total (mg·kg−1)
N
P
K
Pb
Zn
Cu
Cr
4.95
14.5
88.9
11.2
95.0
42.0
60.7
23.8
55.2


### 2.2. Pot Experiments

Two soil amendments were used in this study: mHAP (micrometer hydroxyapatite, bought from Nanjing Emperor Nano Material Co., ltd., China, average particle diameter = 12μm) and nHAP (nanometer particle hydroxyapatite, bought from Nanjing Emperor Nano Material Co., ltd., China, average particle diameter = 60 nm). No Pb, Zn, Cu, and Cr were detected in these two materials. Both soil amendments were applied at two levels, 15 g·kg−1 and 30 g·kg−1. The Pb, Zn, Cu, and Cr were supplied to soil as solutions of PbSO4, CuSO4·5H2O, ZnSO4·7H2O, and KCrO4. The four soil treatments were T0 (without metals added), T1 (250/100 mg·kg−1 Pb/Zn added, resp.), T2 (500/200 mg·kg−1 Pb/Zn added, resp.), T3 (100/25 mg·kg−1 Cu/Cr added, resp.), and T4 (200/50 mg·kg−1 Cu/Cr added, resp.). Altogether, each metal level has mHAP and nHAP treatments. There were four replications in each treatment. The concentration of Pb, Zn, and Cu supplied to the soil exceeded those of the soil environmental quality standards in China, so the metal amended soil can be regarded as slightly metal contaminated (T1 and T3 treatment level) and heavy metal contaminated (T2 and T4 treatment level), respectively. Soil amendments were thoroughly mixed with soil prior to potting nitrogen (6 g·pot−1 soil as NH4NO3) and potassium (6 g·pot−1 soil as KCl). Pots containing 3.0 kg of soil were used in this experiment. Deionized water was supplied to keep the soil water content to about 60% of maximum water holding capacity.The soil was left to equilibrate for 20 days before planting pakchoi (Brassica chinensisL.). Ten pregerminated seeds were sown in each pot. At seven days after emergence, seedlings were thinned to six per pot. The pakchoi was grown in a greenhouse with temperatures between 25 and 30°C. Pakchois were harvested 60 days after emergence.


### 2.3. Metal Analysis

After harvest, the pakchois were removed from the pots and cut into two parts: shoots and roots. The shoots and roots were washed three times by deionized water, then put into the oven to dry at 70°C, and passed through 2 mm sieve for further experiment. The soil samples were taken from the pots after harvesting the vegetables and were air-dried at room temperature, followed by passing through 0.149 mm sieve.Pb, Zn, Cu, and Cr in pakchoi were extracted by using acid digestion mixture (HNO3 and HClO4). The pakchoi samples were heated with HNO3 and HClO4 mixture until the color became clear, filtered, reconstituted to the desired volume, and measured by the inductively coupled plasma optical emission spectrometry (ICP-OES) for Pb, Zn, Cu, and Cr content. For the analysis of Pb, Zn, Cu, and Cr in soil, 0.3 g of homogenized soil samples was digested with HNO3, HClO4, and HF. The samples were heated until the color became clear, dissolved with several drops of 1% HNO3, filtered, diluted to a volume of 50 mL with distilled water, and analyzed for the content of Pb, Zn, Cu, and Cr [6].


### 2.4. Sequential Extraction of Soil Samples

The method of sequential extraction developed by BCR sequential extraction procedure [11] was employed in this study. Each of the chemical fractions was operationally defined as follows: acid soluble fraction: 1 g soil (dry wt) was extracted with 40 mL 0.1 mol·L−1 HOAc, shaking for 16 h; reducible fraction: residue from the acid soluble fraction was extracted with 40 mL 0.5 mol·L−1 NH2OH–HCl (pH 1.5) shaking for 16 h; oxidizable fraction: residue from the reducible fraction was extracted with 10 mL H2O2 for 1 h at 85°C and an additional 10 mL H2O2 for 1 h at 85°C, and then 50 mL 1 mol·L−1 NH4Ac was added, shaking for 16 h; residual fraction: residue from the oxidizable fraction was digested with HNO3–HClO4–HF. After each extraction, separation was performed by centrifugation at 10,000 rpm for 20 min. Metal concentration in the soil solutions was determined by ICP-OES.


### 2.5. Statistical Analysis

The means and standard deviations (SD) were calculated by Excel 2003. Statistical analysis including the analysis of variance was conducted using SPSS version 17.0 software (SPSS Inc., USA) and differences (P<0.05) between means were determined using the Duncan test. The figures were plotted by origin 7.5.


## 2.1. Soil Sample Properties

The soil samples were derived from vegetable gardens. After being air-dried, the soil samples were grounded to pass through a 10 mm sieve for the pot trial. Soil pH was measured in 1 : 2.5 soil water suspensions with a combination pH electrode. Soil organic matter was determined by wet digestion with K2Cr2O7 and H2SO4; available N, P, and K were determined according to standard methods recommended by Lu [10]. Some basic physiochemical properties of the soil and the concentrations of Pb, Zn, Cu, and Cr in this soil were listed in Table 1.Table 1
Basic properties of the soil.
pH
Organic matter (g·kg−1)
Available (mg·kg−1)
Total (mg·kg−1)
N
P
K
Pb
Zn
Cu
Cr
4.95
14.5
88.9
11.2
95.0
42.0
60.7
23.8
55.2


## 2.2. Pot Experiments

Two soil amendments were used in this study: mHAP (micrometer hydroxyapatite, bought from Nanjing Emperor Nano Material Co., ltd., China, average particle diameter = 12μm) and nHAP (nanometer particle hydroxyapatite, bought from Nanjing Emperor Nano Material Co., ltd., China, average particle diameter = 60 nm). No Pb, Zn, Cu, and Cr were detected in these two materials. Both soil amendments were applied at two levels, 15 g·kg−1 and 30 g·kg−1. The Pb, Zn, Cu, and Cr were supplied to soil as solutions of PbSO4, CuSO4·5H2O, ZnSO4·7H2O, and KCrO4. The four soil treatments were T0 (without metals added), T1 (250/100 mg·kg−1 Pb/Zn added, resp.), T2 (500/200 mg·kg−1 Pb/Zn added, resp.), T3 (100/25 mg·kg−1 Cu/Cr added, resp.), and T4 (200/50 mg·kg−1 Cu/Cr added, resp.). Altogether, each metal level has mHAP and nHAP treatments. There were four replications in each treatment. The concentration of Pb, Zn, and Cu supplied to the soil exceeded those of the soil environmental quality standards in China, so the metal amended soil can be regarded as slightly metal contaminated (T1 and T3 treatment level) and heavy metal contaminated (T2 and T4 treatment level), respectively. Soil amendments were thoroughly mixed with soil prior to potting nitrogen (6 g·pot−1 soil as NH4NO3) and potassium (6 g·pot−1 soil as KCl). Pots containing 3.0 kg of soil were used in this experiment. Deionized water was supplied to keep the soil water content to about 60% of maximum water holding capacity.The soil was left to equilibrate for 20 days before planting pakchoi (Brassica chinensisL.). Ten pregerminated seeds were sown in each pot. At seven days after emergence, seedlings were thinned to six per pot. The pakchoi was grown in a greenhouse with temperatures between 25 and 30°C. Pakchois were harvested 60 days after emergence.


## 2.3. Metal Analysis

After harvest, the pakchois were removed from the pots and cut into two parts: shoots and roots. The shoots and roots were washed three times by deionized water, then put into the oven to dry at 70°C, and passed through 2 mm sieve for further experiment. The soil samples were taken from the pots after harvesting the vegetables and were air-dried at room temperature, followed by passing through 0.149 mm sieve.Pb, Zn, Cu, and Cr in pakchoi were extracted by using acid digestion mixture (HNO3 and HClO4). The pakchoi samples were heated with HNO3 and HClO4 mixture until the color became clear, filtered, reconstituted to the desired volume, and measured by the inductively coupled plasma optical emission spectrometry (ICP-OES) for Pb, Zn, Cu, and Cr content. For the analysis of Pb, Zn, Cu, and Cr in soil, 0.3 g of homogenized soil samples was digested with HNO3, HClO4, and HF. The samples were heated until the color became clear, dissolved with several drops of 1% HNO3, filtered, diluted to a volume of 50 mL with distilled water, and analyzed for the content of Pb, Zn, Cu, and Cr [6].


## 2.4. Sequential Extraction of Soil Samples

The method of sequential extraction developed by BCR sequential extraction procedure [11] was employed in this study. Each of the chemical fractions was operationally defined as follows: acid soluble fraction: 1 g soil (dry wt) was extracted with 40 mL 0.1 mol·L−1 HOAc, shaking for 16 h; reducible fraction: residue from the acid soluble fraction was extracted with 40 mL 0.5 mol·L−1 NH2OH–HCl (pH 1.5) shaking for 16 h; oxidizable fraction: residue from the reducible fraction was extracted with 10 mL H2O2 for 1 h at 85°C and an additional 10 mL H2O2 for 1 h at 85°C, and then 50 mL 1 mol·L−1 NH4Ac was added, shaking for 16 h; residual fraction: residue from the oxidizable fraction was digested with HNO3–HClO4–HF. After each extraction, separation was performed by centrifugation at 10,000 rpm for 20 min. Metal concentration in the soil solutions was determined by ICP-OES.


## 2.5. Statistical Analysis

The means and standard deviations (SD) were calculated by Excel 2003. Statistical analysis including the analysis of variance was conducted using SPSS version 17.0 software (SPSS Inc., USA) and differences (P<0.05) between means were determined using the Duncan test. The figures were plotted by origin 7.5.


## 3. Results and Discussions

### 3.1. Effect of mHAP and nHAP on the Biomass of the Pakchoi

The biomass of the pakchoi shoots and roots was significantly decreased by metal application at T2 and T4 treatment levels but increased at T1 and T3 treatment levels compared to the control treatment (Table2). This result corresponds with Chen and Cui [12], who reported that, at low metal contaminated treatment level, the growth of plant can be promoted while, at high metal contaminated treatment level, the growth of plant can be stunted down. Excessive heavy metals, such as Pb, Zn, Cu, and Cr contents in soil, have been reported to inhibit the development of root system of plant, block down the photosynthesis, and led to the decrease of plant yield [13]. The application of mHAP and nHAP both increased the shoots and roots biomass of the pakchoi at all the treatment levels. The result showed that, by supplement of 30 g·kg−1 mHAP, the increment of shoots biomass was 21.98% in T2 treatment level and 25.62% in T4 treatment level as compared to control. As to the nHAP, it was showed that when treated with 30 g·kg−1 nHAP, the increment of shoots biomass was 11.14% in T2 treatment level and 17.79% in T4 treatment level when compared to that of control. It can be found that the application of mHAP and nHAP both increased the shoots and roots biomass of the pakchoi in all treatment levels. This result may be due to the fact that the mHAP and nHAP can release the toxic effect on pakchoi caused by heavy metal treatment, resulting in the increment of the biomass of pakchoi. Another reason may lie in the fact that more phosphate nutrition supplement after phosphate amendments addition can promote the growth of the pakchoi [6]. Furthermore, in this study, mHAP appeared to be more efficient in increasing the biomass of pakchoi in T2 and T4 treatment levels.Table 2
Biomass of pakchoi (Brassica chinensis L.) grown in the uncontaminated soil and contaminated soil with mHAP and nHAP (dry weigh).
Treatment
Shoot (g·pot−1 DW)
Root (g·pot−1 DW)
T0 (CK)
3.61
±
0.26
efg
0.62
±
0.0
4
bc
T0 + 1.5% mHAP
3.96
±
0.28
ij
0.63
±
0.08
cd
T0 + 3% mHAP
3.64
±
0
.
17
fgh
0.62
±
0.18
cd
T0 + 1.5% nHAP
3.83
±
0
.
22
hi
0.64
±
0
.
09
cde
T0 + 3% nHAP
3.60
±
0.31
efg
0.62
±
0.11
bc
T1 (250/100 mg·kg−1 Pb/Zn)
3.96
±
0.25
ij
0.62
±
0.06
bc
T1 + 1.5% mHAP
4.20
±
0
.
10
kl
0.69
±
0.18
efgh
T1 + 3% mHAP
4.31
±
0.53
l
0.82
±
0.09
k
T1 + 1.5% nHAP
4.04
±
0.16
ij
0.65
±
0.13
cdef
T1 + 3% nHAP
4.15
±
0
.
14
jkl
0.66
±
0.10
cdef
T2 (500/200 mg·kg−1 Pb/Zn)
3.23
±
0
.
12
bc
0.56
±
0.11
ab
T2 + 1.5% mHAP
3.39
±
0
.
18
cde
0.65
±
0.07
cdef
T2 + 3% mHAP
3.94
±
0
.
27
ij
0.76
±
0.21
ij
T2 + 1.5% nHAP
3.4
0
±
0
.
43
cde
0.61
±
0.11
bc
T2 + 3% nHAP
3.59
±
0
.
15
efg
0.69
±
0.15
dgh
T3  (100/25 mg·kg−1 Cu/Cr)
3.81
±
0
.
34
hi
0.66
±
0.17
cdef
T3 + 1.5% mHAP
4.01
±
0
.
18
ijk
0.80
±
0.09
jk
T3 + 3% mHAP
4.06
±
0.16
jk
0.82
±
0.11
k
T3 + 1.5% nHAP
3.97
±
0
.
49
ijk
0.74
±
0.15
hij
T3 + 3% nHAP
4.04
±
0.59
ijk
0.78
±
0.08
ijk
T4 (200/50 mg·kg−1 Cu/Cr)
2.81
±
0
.
1
0
a
0.51
±
0.12
a
T4 + 1.5% mHAP
3.27
±
0.25
bc
0.64
±
0.11
cdef
T4 + 3% mHAP
3.53
±
0
.
24
ef
0.71
±
0.18
gh
T4 + 1.5% nHAP
3.08
±
0
.
11
b
0.64
±
0.06
cdef
T4 + 3% nHAP
3.31
±
0
.
19
cd
0.67
±
0.13
cdef
Mean values denoted by the same letter in a column do not differ significantly according to the Duncan test.


### 3.2. Effect of mHAP and nHAP on the Uptake of Pb, Zn, Cu, and Cr by Pakchoi

The application of mHAP and nHAP significantly reduced the concentration of Pb, Zn, Cu, and Cr in the shoots and roots of the pakchoi grown in the contaminated soil (Tables3 and 4). However, the addition of mHAP has better effect than nHAP in heavy metal treatment levels (T2 and T4). The result showed that, by the addition of the 30 g·kg−1 mHAP, the concentrations of Pb, Zn, Cu, and Cr in shoots decreased by 58.1%, 47.3%, 49.4%, and 38.9% in T2 and T4 treatment level, respectively, while the roots reduction was 53.0%, 45.5%, 47.5%, and 44.6% compared to the control. As to the 30 g·kg−1 nHAP application, the reduction in concentration of Pb, Zn, Cu, and Cr in the shoots was 53.4% for Pb, 32.1% for Zn, 32.2% for Cu, and 30.9% for Cr in T2 and T4 treatment levels, respectively, whereas roots Pb, Zn, Cu, and Cr decreased by 42.2% for Pb, 39.3% for Zn, 39.6% for Cu, and 37.5% for Cr when compared with that of control. The result showed that both the mHAP and nHAP can significantly influence Pb, Zn, Cu, and Cr concentrations in the pakchoi vegetable shoots and roots. Similar to the result of pakchoi biomass, the mHAP has better effect on reducing the Pb, Zn content in T2 treatment and Cu, Cr content in T4 treatment in pakchoi shoots and roots. However, it can be observed that the application of 30 g·kg−1 mHAP can significantly reduce the T1 and T3 concentration level of metals in pakchois and therefore produce vegetable with Pb, Zn, Cu, and Cr concentrations under the Chinese national food safety standard (GB2762-2005, in China) level.Table 3
Concentration of Pb and Zn in pakchoi (Brassica chinensis L.) grown in Pb-Zn multiple metal-contaminated soil in pot culture receiving mHAP and nHAP amendments (dry weigh).
Pb
Zn
Shoot(mg·kg−1)
Root(mg·kg−1)
Shoot(mg·kg−1)
Root(mg·kg−1)
T0 (CK)
0.40
±
0.02
a
2.93
±
0.15
a
28.05
±
1.66
bcd
38.29
±
1.94
f
T0 + 1.5% mHAP
0.34
±
0.02
a
2.62
±
0.12
a
24.54
±
0.99
b
31.88
±
1.87
d
T0 + 3% mHAP
0.32
±
0.03
a
2.25
±
0.10
a
18.45
±
1.24
a
24.90
±
1.99
a
T0+ 1.5% nHAP
0.34
±
0.01
a
2.43
±
0.09
a
24.90
±
1.02
bc
31.22
±
2.93
cd
T0 + 3% nHAP
0.30
±
0.02
a
2.22
±
0.07
a
20.35
±
1.73
a
27.23
±
2.17
b
T1
4.45
±
0.23
d
26.92
±
0.76
de
40.91
±
2.36
f
48.53
±
2.05
g
T1 + 1.5% mHAP
3.48
±
0.11
c
20.20
±
1.54
c
30.47
±
1.41
de
32.91
±
1.07
d
T1 + 3% mHAP
1.80
±
0.08
b
15.08
±
0.88
b
22.52
±
0.23
a
29.31
±
2.44
bc
T1 + 1.5% nHAP
3.42
±
0.21
c
22.14
±
1.32
c
32.24
±
2.00
e
35.53
±
2.82
e
T1 + 3% nHAP
2.16
±
0.08
b
16.39
±
1.00
b
25.80
±
1.25
bc
31.39
±
1.63
cd
T2
12.15
±
0.77
h
53.94
±
2.69
h
51.02
±
3.58
g
86.84
±
5.85
k
T2 + 1.5% mHAP
7.21
±
0.62
g
28.25
±
1.36
e
31.63
±
1.97
e
59.50
±
2.55
i
T2 + 3% mHAP
5.09
±
0.39
e
25.35
±
1.82
d
26.89
±
1.55
bc
47.37
±
3.43
g
T2 + 1.5% nHAP
7.59
±
0.56
g
37.67
±
2.04
g
38.44
±
1.61
f
63.83
±
5.01
j
T2 + 3% nHAP
5.66
±
0.50
f
31.20
±
1.91
f
31.59
±
1.26
e
52.70
±
3.38
h
Mean values denoted by the same letter in a column do not differ significantly according to the Duncan test.Table 4
Concentration of Cu and Cr in pakchoi (Brassica chinensis L.) grown in Cu-Cr multiple metal-contaminated soil in pot culture receiving mHAP and nHAP amendments.
Cu
Cr
Shoot(mg·kg−1)
Root(mg·kg−1)
Shoot(mg·kg−1)
Root(mg·kg−1)
T0 (CK)
6.32
±
0.36
a
9.72
±
0.54
a
1.94
±
0.08
b
3.54
±
0.14
a
T0 + 1.5% mHAP
5.90
±
0.20
a
9.51
±
0.77
a
1.58
±
0.06
ab
2.89
±
0.09
a
T0 + 3% mHAP
4.78
±
0.29
a
7.68
±
0.64
a
1.45
±
0.06
a
2.53
±
0.07
a
T0 + 1.5% nHAP
5.84
±
0.41
a
8.60
±
0.26
a
1.75
±
0.05
ab
2.96
±
0.20
a
T0 + 3% nHAP
5.32
±
0.35
a
7.94
±
0.81
a
1.51
±
0.11
ab
2.67
±
0.18
a
T3
17.16
±
0.76
f
33.75
±
1.53
d
4.25
±
0.20
e
15.25
±
0.78
e
T3 + 1.5% mHAP
13.20
±
0.79
cd
2
3
.
89
±
1.44
c
3.07
±
0.26
d
10.34
±
0.65
c
T3 + 3% mHAP
10.06
±
0.42
b
19.61
±
0.86
b
2.65
±
0.15
c
9.44
±
0.53
b
T3 + 1.5% nHAP
14.04
±
1.38
de
24.19
±
0.99
c
3.28
±
0.23
d
13.17
±
0.10
d
T3 + 3% nHAP
12.14
±
0.74
c
20.98
±
1.30
b
2.99
±
0.17
cd
9.49
±
0.04
b
T4
30.39
±
1.90
i
76.00
±
4.11
h
6.76
±
0.48
h
34.54
±
1.87
j
T4 + 1.5% mHAP
20.64
±
1.36
h
53.22
±
2.76
g
5.02
±
0.17
fg
22.66
±
2.33
h
T4 + 3% mHAP
15.37
±
0.85
e
39.92
±
2.53
e
4.13
±
0.26
e
19.14
±
0.86
f
T4 + 1.5% nHAP
22.06
±
1.03
h
54.90
±
3.53
g
5.30
±
0.32
g
25.35
±
1.92
i
T4 + 3% nHAP
18.77
±
1.12
g
45.88
±
1.92
f
4.67
±
0.35
f
21.60
±
2.90
g
Mean values denoted by the same letter in a column do not differ significantly according to the Duncan test.


### 3.3. Effect of mHAP and nHAP on the pH of the Soil

Some researchers [14] suggested that the pH was one of the most important parameters affected metal bioavailability to plants. In the low pH (pH < 5) condition, the metal in soil has higher solubility. As a result, more metal ion released to the soil solution. The metal therefore was more bioavailable to the plants. The application of HAP amendment can increase the soil pH and reduce the metal bioavailability, especially in the low pH soil conditions. This study indicated that the supplement of mHAP and nHAP both significantly increased the soil pH compared to the unamended metals contaminated soil (Table 5). However, it can be observed that the mHAP had better effect than nHAP in increasing the pH of each treatment level, especially in 30 g·kg−1 application rate. The result showed that when compared with the contaminated soil without adding amendment, after applying for 30 g·kg−1 mHAP, the pH value was raised by 0.99 in T1 treatment level, 1.08 in T2 treatment level, 0.88 in T3 treatment level, and 1.22 in T4 treatment level. As to the nHAP, the enhancement of pH value was 0.75 in T1 treatment level, 0.58 in T2 treatment level, 0.63 in T3 treatment level, and 0.90 in T4 treatment level when compared with the contaminated soil without adding amendment.Table 5
pH value in the tested soil as affected by mHAP and nHAP amendments.
Treatment
pH
T0 (CK)
4.95
T0 + 1.5% mHAP
5.46
T0 + 3% mHAP
5.99
T0 + 1.5% nHAP
5.20
T0 + 3% nHAP
5.76
T1
5.08
T1 + 1.5% mHAP
5.76
T1 + 3% mHAP
6.07
T1 + 1.5% nHAP
5.42
T1 + 3% nHAP
5.83
T3
5.11
T3 + 1.5% mHAP
5.60
T3 + 3% mHAP
5.99
T3 + 1.5% nHAP
5.18
T3 + 3% nHAP
5.74
T2
5.16
T2 + 1.5% mHAP
5.72
T2 + 3% mHAP
6.24
T2 + 1.5% nHAP
5.45
T2 + 3% nHAP
5.74
T4
4.97
T4 + 1.5% mHAP
5.68
T4 + 3% mHAP
6.19
T4 + 1.5% nHAP
5.39
T4 + 3% nHAP
5.87pH was an important parameter which affected metal immobilization and dissolution in soil [15]. The metal solubility and mobility increased with the decrease of pH. In contrast, when the soil pH increased, the solubility and mobility of metal in soil went down. Bolisson et al. [16] reported that the application of HAP can increase the soil pH value. This was attributed to the fact that the dissolution of HAP in soil solution can consume H+, resulting in the increase of soil pH:
(1)Ca10(PO4)6(OH)2+14H+=10Ca2++6H2PO4-+2H2OIt was reported that when HAP was dissolved in deionized water and 0.1 mol/L KNO3 solution, the dissolution rate of HAP mainly depended on pH [17, 18]. Soil solution was more complicated when compared with deionized water or single electrolyte solution. Generally speaking, in low pH soil condition, the dissolution rate of HAP was more faster than in neutral and alkali soil. As in the acidic soil condition, the PO43- in hydroxyapatite had higher efficiency to dissolve and release to the soil solution. In this study, the application of mHAP had better effect in increasing the soil pH than nHAP, suggesting that mHAP has a larger dissolution rate than nHAP.


### 3.4. Speciation of Soil Pb, Zn, Cu, and Cr

The distribution of Pb, Zn, Cu, and Cr in the uncontaminated soil and metal-contaminated soil as analyzed by the BCR sequential extraction method was shown in Figure1. The metal (Pb, Zn, Cu, and Cr) in the treatments without mHAP and nHAP was mainly associated with the nonresidual fraction. The percentage of Pb, Zn, and Cu bound with the nonresidual fraction (including acid soluble fraction, reducible fraction, and oxidizable fraction) accounted for over 74.1% for Pb and 76.3% for Zn in T1 treatment level and 79.72% for Pb and 62.96% for Zn in T2 treatment level, 88.1% for Cu and 60.73% for Cr in T3 treatment level, and 88.12% for Cu and 56.47% for Cr in T4 treatment level, respectively. This indicated that a substantial fraction of Pb, Zn, Cu, and Cr in the contaminated soil without amendment may be available for pakchoi to uptake. As to the HAP amended soil, both mHAP and nHAP translocated nonresidual fractions of Pb, Zn, Cu, and Cr to the residual fraction. For instance, by addition of 30 g kg−1 mHAP, the reduction in the nonresidual fraction was 36.0% for Pb and 34.9% for Zn in T1 treatment level, 36.1% for Pb and 27.5% for Zn in T2 treatment level, 32.5% for Cu and 26.8% for Cr in T3 treatment level, and 26.6% for Cu and 20.0% for Cr in T4 treatment level. The reduction in the nonresidual fraction was 29.8% for Pb and 29.4% for Zn in T1 treatment level, 20.7% for Pb and 27.5% for Zn in T2 treatment level, 23.1% for Cu and 21.9% for Cr in T3 treatment level, and 17.1% for Cu and 14.8% for Cr in T4 treatment level by addition of 30 g kg−1 nHAP treatment.Relative percentages of Pb, Zn, Cu, and Cr in each fraction of the soils from the CK, mHAP, and nHAP treated pots.
(a)
(b)
(c)
(d)The result showed that nonresidual fraction of Pb, Zn, Cu, and Cr decreased with the increase of soil pH, hinting that the pH values play an important role in decreasing the nonresidual fraction. The increase of pH values induced by HAP favored the precipitation of heavy metals. In addition, Gray et al. [19] found that the increase of soil pH values increased the negative charges of variably charged colloids in soil, such as organic matter, clays, Fe and Al oxides, and silicon oxides, resulting in stronger sorption and precipitation of heavy metals and hence lower soluble metal concentrations in soil. In this study, it can be found that mHAP has better effect on transforming metals from the nonresidual to the residual fraction, which was consistent with the result of soil pH changed by mHAP and nHAP, indicating that larger soil pH values with mHAP addition than nHAP were the main reason for the superior ability of immobilization Pb, Zn, Cu, and Cr in soil of mHAP.In this paper, we identified the effectiveness of mHAP and nHAP to reduce the amounts of heavy metals in contaminated soil. The efficiency ofin situ remediation of metal-contaminated soils can be evaluated by using fractionation procedures; the more effective the treatment, the greater the amount of metals transferred from the nonresidual to the residual fraction [20, 21]. BCR sequential extraction procedures were widely used to assess the bioavailability and mobility of heavy metals in soils as well as the efficacy of decontamination amendment. The nonresidual metal fractionation, which includes acid soluble (weakly bound with organic matter and carbonates fraction), reducible (iron and manganese oxides fraction), and oxidizable (organically bound and sulfide fraction) fractions, is more mobile and is considered to have a higher bioavailability as compared with the residual fraction [22, 23]. In the current study, both mHAP and nHAP were highly capable of modifying Pb, Zn, Cu, and Cr in contaminated soils, with a concurrent increase in the residual fractionation and a decrease in the nonresidual fractionation, especially the acid soluble fractionation. Moreover, mHAP and nHAP were more effective in transforming the nonresidual fractionation of Pb than the other three heavy metals, as expected. One of the most important effects of HAP modification is the formation of pyromorphite from Pb, thus resulting in the transformation of Pb from nonresidual fractions to the residual fraction [24]. This study confirmed that the supplementation of both mHAP and nHAP significantly enhanced the residual fraction of Pb in soils, corresponding to a reduction of Pb in pakchoi shoots and roots.We also found that the addition of mHAP and nHAP decreased the nonresidual fraction of Cu, Zn, and Cr in the soil. However, the immobilization efficacy was lower than Pb. We hypothesized two reasons for this phenomenon. Firstly, the solubility products of Cu, Zn, and Cr phosphate are known to be much greater than that of Pb phosphate. However, hopeite [Zn3(PO4)2], Cu3(PO4)2, and Cr2(PO4)7 are much more soluble than pyromorphite. As such, Cu, Zn, and Cr phosphate may not control the solubility of these heavy metals in this case [6]. And secondly, we believe that the primary mechanism is likely due to the adsorption potential of the surface of HAP. For instance, Cao et al. [25] reported that the application of HAP in Pb, Cu, and Zn contaminated soil and showed that 78% of Pb that reacted with HAP was formed of pyromorphite. Meanwhile, only 25% of Cu and 5% of Zn were formed of Cu2(PO4)3 and Zn2(PO4) and 75% Cu and 95% Zn were adsorbed upon the surface of HAP. Results from this study confirmed that mHAP and nHAP had great ability for reducing Pb bioavailability and also for inhibiting the uptake of Pb to a greater degree than Zn, Cu, and Cr. However, mHAP was more capable of decreasing the overall amount of metals taken up by the pakchoi plant.The reduction of Pb content in the pakchoi shoots and roots can be attributed to the formation of pyromorphite in the soil. As to the decrease of Zn, Cu, and Cr in pakchoi shoots and roots, the main reason involved of Zn, Cu and Cr adsorption on the HAP and the higher solubility of [Zn3(PO4)2], Cd3(PO4)2 and Cr2(PO4)7 than pyromorphite. Moreover, the reduction of Pb, Zn, Cu, and Cr content in the pakchoi shoots and roots was as follows: Pb>Zn≈Cu>Cr. These results are consistent with the sequence in the reduction of Pb, Zn, Cu, and Cr of the nonresidual fraction found in contaminated soil, suggesting that the nonresidual fraction of heavy metals can readily be taken up by the pakchoi plant and also shows the highest levels of bioavailability for the pakchoi.Many studies have been conducted in recent years focused on the heavy metal remediation potential of nanomaterials in contaminated soil [26, 27]. Phosphate-based nanoparticles have been found to be one of the most effective nanomaterials for the reclamation of heavy metal contaminated soil. For instance, Liu and Zhao [28] reported that the application of iron phosphate nanoparticles in Pb-contaminated soil can effectively reduce the leachability and bioavailability of Pb2+ in soil. Moreover, Liu [29] also reported an effective reclamation of a lead-contaminated soil using synthesized apatite nanoparticles. Their experimental results clearly showed that the apatite nanoparticles solution could significantly reduce the TCLP-leachable Pb fraction in Pb-contaminated soil by 9.56% to 66.43%. Many studies have suggested that nanomaterials are superior to traditional modifications using commonly particle sizes for soil remediation due to nanomaterials having a higher reactivity and a greater ability for absorption and for its relatively easy delivery methods. Theoretically, in this study a larger amount of Pb, Zn, Cu, and Cr was able to be immobilized by nHAP, likely due to its smaller particle sizes yet larger surface area, as compared to mHAP. However, we found that mHAP was more effective than nHAP in immobilizing Pb, Zn, Cu, and Cr. Furthermore, the pH value of the soil was more greatly enhanced by mHAP. Gilbert et al. [30] and Cui et al. [18] suggested that nanomaterials can easily aggregate, leading to an alteration to their surface sorption and ability to migrate while decreasing their dissolution rates. mHAP has a larger particle size, as compared to nHAP making it much more difficult for mHAP to aggregate. Therefore, we hypothesized that the higher dissolution rate was the primary reason for the increases in the pH value and for its increased immobilization effects. Nevertheless, further studies are needed in order to verify this hypothesis.


## 3.1. Effect of mHAP and nHAP on the Biomass of the Pakchoi

The biomass of the pakchoi shoots and roots was significantly decreased by metal application at T2 and T4 treatment levels but increased at T1 and T3 treatment levels compared to the control treatment (Table2). This result corresponds with Chen and Cui [12], who reported that, at low metal contaminated treatment level, the growth of plant can be promoted while, at high metal contaminated treatment level, the growth of plant can be stunted down. Excessive heavy metals, such as Pb, Zn, Cu, and Cr contents in soil, have been reported to inhibit the development of root system of plant, block down the photosynthesis, and led to the decrease of plant yield [13]. The application of mHAP and nHAP both increased the shoots and roots biomass of the pakchoi at all the treatment levels. The result showed that, by supplement of 30 g·kg−1 mHAP, the increment of shoots biomass was 21.98% in T2 treatment level and 25.62% in T4 treatment level as compared to control. As to the nHAP, it was showed that when treated with 30 g·kg−1 nHAP, the increment of shoots biomass was 11.14% in T2 treatment level and 17.79% in T4 treatment level when compared to that of control. It can be found that the application of mHAP and nHAP both increased the shoots and roots biomass of the pakchoi in all treatment levels. This result may be due to the fact that the mHAP and nHAP can release the toxic effect on pakchoi caused by heavy metal treatment, resulting in the increment of the biomass of pakchoi. Another reason may lie in the fact that more phosphate nutrition supplement after phosphate amendments addition can promote the growth of the pakchoi [6]. Furthermore, in this study, mHAP appeared to be more efficient in increasing the biomass of pakchoi in T2 and T4 treatment levels.Table 2
Biomass of pakchoi (Brassica chinensis L.) grown in the uncontaminated soil and contaminated soil with mHAP and nHAP (dry weigh).
Treatment
Shoot (g·pot−1 DW)
Root (g·pot−1 DW)
T0 (CK)
3.61
±
0.26
efg
0.62
±
0.0
4
bc
T0 + 1.5% mHAP
3.96
±
0.28
ij
0.63
±
0.08
cd
T0 + 3% mHAP
3.64
±
0
.
17
fgh
0.62
±
0.18
cd
T0 + 1.5% nHAP
3.83
±
0
.
22
hi
0.64
±
0
.
09
cde
T0 + 3% nHAP
3.60
±
0.31
efg
0.62
±
0.11
bc
T1 (250/100 mg·kg−1 Pb/Zn)
3.96
±
0.25
ij
0.62
±
0.06
bc
T1 + 1.5% mHAP
4.20
±
0
.
10
kl
0.69
±
0.18
efgh
T1 + 3% mHAP
4.31
±
0.53
l
0.82
±
0.09
k
T1 + 1.5% nHAP
4.04
±
0.16
ij
0.65
±
0.13
cdef
T1 + 3% nHAP
4.15
±
0
.
14
jkl
0.66
±
0.10
cdef
T2 (500/200 mg·kg−1 Pb/Zn)
3.23
±
0
.
12
bc
0.56
±
0.11
ab
T2 + 1.5% mHAP
3.39
±
0
.
18
cde
0.65
±
0.07
cdef
T2 + 3% mHAP
3.94
±
0
.
27
ij
0.76
±
0.21
ij
T2 + 1.5% nHAP
3.4
0
±
0
.
43
cde
0.61
±
0.11
bc
T2 + 3% nHAP
3.59
±
0
.
15
efg
0.69
±
0.15
dgh
T3  (100/25 mg·kg−1 Cu/Cr)
3.81
±
0
.
34
hi
0.66
±
0.17
cdef
T3 + 1.5% mHAP
4.01
±
0
.
18
ijk
0.80
±
0.09
jk
T3 + 3% mHAP
4.06
±
0.16
jk
0.82
±
0.11
k
T3 + 1.5% nHAP
3.97
±
0
.
49
ijk
0.74
±
0.15
hij
T3 + 3% nHAP
4.04
±
0.59
ijk
0.78
±
0.08
ijk
T4 (200/50 mg·kg−1 Cu/Cr)
2.81
±
0
.
1
0
a
0.51
±
0.12
a
T4 + 1.5% mHAP
3.27
±
0.25
bc
0.64
±
0.11
cdef
T4 + 3% mHAP
3.53
±
0
.
24
ef
0.71
±
0.18
gh
T4 + 1.5% nHAP
3.08
±
0
.
11
b
0.64
±
0.06
cdef
T4 + 3% nHAP
3.31
±
0
.
19
cd
0.67
±
0.13
cdef
Mean values denoted by the same letter in a column do not differ significantly according to the Duncan test.


## 3.2. Effect of mHAP and nHAP on the Uptake of Pb, Zn, Cu, and Cr by Pakchoi

The application of mHAP and nHAP significantly reduced the concentration of Pb, Zn, Cu, and Cr in the shoots and roots of the pakchoi grown in the contaminated soil (Tables3 and 4). However, the addition of mHAP has better effect than nHAP in heavy metal treatment levels (T2 and T4). The result showed that, by the addition of the 30 g·kg−1 mHAP, the concentrations of Pb, Zn, Cu, and Cr in shoots decreased by 58.1%, 47.3%, 49.4%, and 38.9% in T2 and T4 treatment level, respectively, while the roots reduction was 53.0%, 45.5%, 47.5%, and 44.6% compared to the control. As to the 30 g·kg−1 nHAP application, the reduction in concentration of Pb, Zn, Cu, and Cr in the shoots was 53.4% for Pb, 32.1% for Zn, 32.2% for Cu, and 30.9% for Cr in T2 and T4 treatment levels, respectively, whereas roots Pb, Zn, Cu, and Cr decreased by 42.2% for Pb, 39.3% for Zn, 39.6% for Cu, and 37.5% for Cr when compared with that of control. The result showed that both the mHAP and nHAP can significantly influence Pb, Zn, Cu, and Cr concentrations in the pakchoi vegetable shoots and roots. Similar to the result of pakchoi biomass, the mHAP has better effect on reducing the Pb, Zn content in T2 treatment and Cu, Cr content in T4 treatment in pakchoi shoots and roots. However, it can be observed that the application of 30 g·kg−1 mHAP can significantly reduce the T1 and T3 concentration level of metals in pakchois and therefore produce vegetable with Pb, Zn, Cu, and Cr concentrations under the Chinese national food safety standard (GB2762-2005, in China) level.Table 3
Concentration of Pb and Zn in pakchoi (Brassica chinensis L.) grown in Pb-Zn multiple metal-contaminated soil in pot culture receiving mHAP and nHAP amendments (dry weigh).
Pb
Zn
Shoot(mg·kg−1)
Root(mg·kg−1)
Shoot(mg·kg−1)
Root(mg·kg−1)
T0 (CK)
0.40
±
0.02
a
2.93
±
0.15
a
28.05
±
1.66
bcd
38.29
±
1.94
f
T0 + 1.5% mHAP
0.34
±
0.02
a
2.62
±
0.12
a
24.54
±
0.99
b
31.88
±
1.87
d
T0 + 3% mHAP
0.32
±
0.03
a
2.25
±
0.10
a
18.45
±
1.24
a
24.90
±
1.99
a
T0+ 1.5% nHAP
0.34
±
0.01
a
2.43
±
0.09
a
24.90
±
1.02
bc
31.22
±
2.93
cd
T0 + 3% nHAP
0.30
±
0.02
a
2.22
±
0.07
a
20.35
±
1.73
a
27.23
±
2.17
b
T1
4.45
±
0.23
d
26.92
±
0.76
de
40.91
±
2.36
f
48.53
±
2.05
g
T1 + 1.5% mHAP
3.48
±
0.11
c
20.20
±
1.54
c
30.47
±
1.41
de
32.91
±
1.07
d
T1 + 3% mHAP
1.80
±
0.08
b
15.08
±
0.88
b
22.52
±
0.23
a
29.31
±
2.44
bc
T1 + 1.5% nHAP
3.42
±
0.21
c
22.14
±
1.32
c
32.24
±
2.00
e
35.53
±
2.82
e
T1 + 3% nHAP
2.16
±
0.08
b
16.39
±
1.00
b
25.80
±
1.25
bc
31.39
±
1.63
cd
T2
12.15
±
0.77
h
53.94
±
2.69
h
51.02
±
3.58
g
86.84
±
5.85
k
T2 + 1.5% mHAP
7.21
±
0.62
g
28.25
±
1.36
e
31.63
±
1.97
e
59.50
±
2.55
i
T2 + 3% mHAP
5.09
±
0.39
e
25.35
±
1.82
d
26.89
±
1.55
bc
47.37
±
3.43
g
T2 + 1.5% nHAP
7.59
±
0.56
g
37.67
±
2.04
g
38.44
±
1.61
f
63.83
±
5.01
j
T2 + 3% nHAP
5.66
±
0.50
f
31.20
±
1.91
f
31.59
±
1.26
e
52.70
±
3.38
h
Mean values denoted by the same letter in a column do not differ significantly according to the Duncan test.Table 4
Concentration of Cu and Cr in pakchoi (Brassica chinensis L.) grown in Cu-Cr multiple metal-contaminated soil in pot culture receiving mHAP and nHAP amendments.
Cu
Cr
Shoot(mg·kg−1)
Root(mg·kg−1)
Shoot(mg·kg−1)
Root(mg·kg−1)
T0 (CK)
6.32
±
0.36
a
9.72
±
0.54
a
1.94
±
0.08
b
3.54
±
0.14
a
T0 + 1.5% mHAP
5.90
±
0.20
a
9.51
±
0.77
a
1.58
±
0.06
ab
2.89
±
0.09
a
T0 + 3% mHAP
4.78
±
0.29
a
7.68
±
0.64
a
1.45
±
0.06
a
2.53
±
0.07
a
T0 + 1.5% nHAP
5.84
±
0.41
a
8.60
±
0.26
a
1.75
±
0.05
ab
2.96
±
0.20
a
T0 + 3% nHAP
5.32
±
0.35
a
7.94
±
0.81
a
1.51
±
0.11
ab
2.67
±
0.18
a
T3
17.16
±
0.76
f
33.75
±
1.53
d
4.25
±
0.20
e
15.25
±
0.78
e
T3 + 1.5% mHAP
13.20
±
0.79
cd
2
3
.
89
±
1.44
c
3.07
±
0.26
d
10.34
±
0.65
c
T3 + 3% mHAP
10.06
±
0.42
b
19.61
±
0.86
b
2.65
±
0.15
c
9.44
±
0.53
b
T3 + 1.5% nHAP
14.04
±
1.38
de
24.19
±
0.99
c
3.28
±
0.23
d
13.17
±
0.10
d
T3 + 3% nHAP
12.14
±
0.74
c
20.98
±
1.30
b
2.99
±
0.17
cd
9.49
±
0.04
b
T4
30.39
±
1.90
i
76.00
±
4.11
h
6.76
±
0.48
h
34.54
±
1.87
j
T4 + 1.5% mHAP
20.64
±
1.36
h
53.22
±
2.76
g
5.02
±
0.17
fg
22.66
±
2.33
h
T4 + 3% mHAP
15.37
±
0.85
e
39.92
±
2.53
e
4.13
±
0.26
e
19.14
±
0.86
f
T4 + 1.5% nHAP
22.06
±
1.03
h
54.90
±
3.53
g
5.30
±
0.32
g
25.35
±
1.92
i
T4 + 3% nHAP
18.77
±
1.12
g
45.88
±
1.92
f
4.67
±
0.35
f
21.60
±
2.90
g
Mean values denoted by the same letter in a column do not differ significantly according to the Duncan test.


## 3.3. Effect of mHAP and nHAP on the pH of the Soil

Some researchers [14] suggested that the pH was one of the most important parameters affected metal bioavailability to plants. In the low pH (pH < 5) condition, the metal in soil has higher solubility. As a result, more metal ion released to the soil solution. The metal therefore was more bioavailable to the plants. The application of HAP amendment can increase the soil pH and reduce the metal bioavailability, especially in the low pH soil conditions. This study indicated that the supplement of mHAP and nHAP both significantly increased the soil pH compared to the unamended metals contaminated soil (Table 5). However, it can be observed that the mHAP had better effect than nHAP in increasing the pH of each treatment level, especially in 30 g·kg−1 application rate. The result showed that when compared with the contaminated soil without adding amendment, after applying for 30 g·kg−1 mHAP, the pH value was raised by 0.99 in T1 treatment level, 1.08 in T2 treatment level, 0.88 in T3 treatment level, and 1.22 in T4 treatment level. As to the nHAP, the enhancement of pH value was 0.75 in T1 treatment level, 0.58 in T2 treatment level, 0.63 in T3 treatment level, and 0.90 in T4 treatment level when compared with the contaminated soil without adding amendment.Table 5
pH value in the tested soil as affected by mHAP and nHAP amendments.
Treatment
pH
T0 (CK)
4.95
T0 + 1.5% mHAP
5.46
T0 + 3% mHAP
5.99
T0 + 1.5% nHAP
5.20
T0 + 3% nHAP
5.76
T1
5.08
T1 + 1.5% mHAP
5.76
T1 + 3% mHAP
6.07
T1 + 1.5% nHAP
5.42
T1 + 3% nHAP
5.83
T3
5.11
T3 + 1.5% mHAP
5.60
T3 + 3% mHAP
5.99
T3 + 1.5% nHAP
5.18
T3 + 3% nHAP
5.74
T2
5.16
T2 + 1.5% mHAP
5.72
T2 + 3% mHAP
6.24
T2 + 1.5% nHAP
5.45
T2 + 3% nHAP
5.74
T4
4.97
T4 + 1.5% mHAP
5.68
T4 + 3% mHAP
6.19
T4 + 1.5% nHAP
5.39
T4 + 3% nHAP
5.87pH was an important parameter which affected metal immobilization and dissolution in soil [15]. The metal solubility and mobility increased with the decrease of pH. In contrast, when the soil pH increased, the solubility and mobility of metal in soil went down. Bolisson et al. [16] reported that the application of HAP can increase the soil pH value. This was attributed to the fact that the dissolution of HAP in soil solution can consume H+, resulting in the increase of soil pH:
(1)Ca10(PO4)6(OH)2+14H+=10Ca2++6H2PO4-+2H2OIt was reported that when HAP was dissolved in deionized water and 0.1 mol/L KNO3 solution, the dissolution rate of HAP mainly depended on pH [17, 18]. Soil solution was more complicated when compared with deionized water or single electrolyte solution. Generally speaking, in low pH soil condition, the dissolution rate of HAP was more faster than in neutral and alkali soil. As in the acidic soil condition, the PO43- in hydroxyapatite had higher efficiency to dissolve and release to the soil solution. In this study, the application of mHAP had better effect in increasing the soil pH than nHAP, suggesting that mHAP has a larger dissolution rate than nHAP.


## 3.4. Speciation of Soil Pb, Zn, Cu, and Cr

The distribution of Pb, Zn, Cu, and Cr in the uncontaminated soil and metal-contaminated soil as analyzed by the BCR sequential extraction method was shown in Figure1. The metal (Pb, Zn, Cu, and Cr) in the treatments without mHAP and nHAP was mainly associated with the nonresidual fraction. The percentage of Pb, Zn, and Cu bound with the nonresidual fraction (including acid soluble fraction, reducible fraction, and oxidizable fraction) accounted for over 74.1% for Pb and 76.3% for Zn in T1 treatment level and 79.72% for Pb and 62.96% for Zn in T2 treatment level, 88.1% for Cu and 60.73% for Cr in T3 treatment level, and 88.12% for Cu and 56.47% for Cr in T4 treatment level, respectively. This indicated that a substantial fraction of Pb, Zn, Cu, and Cr in the contaminated soil without amendment may be available for pakchoi to uptake. As to the HAP amended soil, both mHAP and nHAP translocated nonresidual fractions of Pb, Zn, Cu, and Cr to the residual fraction. For instance, by addition of 30 g kg−1 mHAP, the reduction in the nonresidual fraction was 36.0% for Pb and 34.9% for Zn in T1 treatment level, 36.1% for Pb and 27.5% for Zn in T2 treatment level, 32.5% for Cu and 26.8% for Cr in T3 treatment level, and 26.6% for Cu and 20.0% for Cr in T4 treatment level. The reduction in the nonresidual fraction was 29.8% for Pb and 29.4% for Zn in T1 treatment level, 20.7% for Pb and 27.5% for Zn in T2 treatment level, 23.1% for Cu and 21.9% for Cr in T3 treatment level, and 17.1% for Cu and 14.8% for Cr in T4 treatment level by addition of 30 g kg−1 nHAP treatment.Relative percentages of Pb, Zn, Cu, and Cr in each fraction of the soils from the CK, mHAP, and nHAP treated pots.
(a)
(b)
(c)
(d)The result showed that nonresidual fraction of Pb, Zn, Cu, and Cr decreased with the increase of soil pH, hinting that the pH values play an important role in decreasing the nonresidual fraction. The increase of pH values induced by HAP favored the precipitation of heavy metals. In addition, Gray et al. [19] found that the increase of soil pH values increased the negative charges of variably charged colloids in soil, such as organic matter, clays, Fe and Al oxides, and silicon oxides, resulting in stronger sorption and precipitation of heavy metals and hence lower soluble metal concentrations in soil. In this study, it can be found that mHAP has better effect on transforming metals from the nonresidual to the residual fraction, which was consistent with the result of soil pH changed by mHAP and nHAP, indicating that larger soil pH values with mHAP addition than nHAP were the main reason for the superior ability of immobilization Pb, Zn, Cu, and Cr in soil of mHAP.In this paper, we identified the effectiveness of mHAP and nHAP to reduce the amounts of heavy metals in contaminated soil. The efficiency ofin situ remediation of metal-contaminated soils can be evaluated by using fractionation procedures; the more effective the treatment, the greater the amount of metals transferred from the nonresidual to the residual fraction [20, 21]. BCR sequential extraction procedures were widely used to assess the bioavailability and mobility of heavy metals in soils as well as the efficacy of decontamination amendment. The nonresidual metal fractionation, which includes acid soluble (weakly bound with organic matter and carbonates fraction), reducible (iron and manganese oxides fraction), and oxidizable (organically bound and sulfide fraction) fractions, is more mobile and is considered to have a higher bioavailability as compared with the residual fraction [22, 23]. In the current study, both mHAP and nHAP were highly capable of modifying Pb, Zn, Cu, and Cr in contaminated soils, with a concurrent increase in the residual fractionation and a decrease in the nonresidual fractionation, especially the acid soluble fractionation. Moreover, mHAP and nHAP were more effective in transforming the nonresidual fractionation of Pb than the other three heavy metals, as expected. One of the most important effects of HAP modification is the formation of pyromorphite from Pb, thus resulting in the transformation of Pb from nonresidual fractions to the residual fraction [24]. This study confirmed that the supplementation of both mHAP and nHAP significantly enhanced the residual fraction of Pb in soils, corresponding to a reduction of Pb in pakchoi shoots and roots.We also found that the addition of mHAP and nHAP decreased the nonresidual fraction of Cu, Zn, and Cr in the soil. However, the immobilization efficacy was lower than Pb. We hypothesized two reasons for this phenomenon. Firstly, the solubility products of Cu, Zn, and Cr phosphate are known to be much greater than that of Pb phosphate. However, hopeite [Zn3(PO4)2], Cu3(PO4)2, and Cr2(PO4)7 are much more soluble than pyromorphite. As such, Cu, Zn, and Cr phosphate may not control the solubility of these heavy metals in this case [6]. And secondly, we believe that the primary mechanism is likely due to the adsorption potential of the surface of HAP. For instance, Cao et al. [25] reported that the application of HAP in Pb, Cu, and Zn contaminated soil and showed that 78% of Pb that reacted with HAP was formed of pyromorphite. Meanwhile, only 25% of Cu and 5% of Zn were formed of Cu2(PO4)3 and Zn2(PO4) and 75% Cu and 95% Zn were adsorbed upon the surface of HAP. Results from this study confirmed that mHAP and nHAP had great ability for reducing Pb bioavailability and also for inhibiting the uptake of Pb to a greater degree than Zn, Cu, and Cr. However, mHAP was more capable of decreasing the overall amount of metals taken up by the pakchoi plant.The reduction of Pb content in the pakchoi shoots and roots can be attributed to the formation of pyromorphite in the soil. As to the decrease of Zn, Cu, and Cr in pakchoi shoots and roots, the main reason involved of Zn, Cu and Cr adsorption on the HAP and the higher solubility of [Zn3(PO4)2], Cd3(PO4)2 and Cr2(PO4)7 than pyromorphite. Moreover, the reduction of Pb, Zn, Cu, and Cr content in the pakchoi shoots and roots was as follows: Pb>Zn≈Cu>Cr. These results are consistent with the sequence in the reduction of Pb, Zn, Cu, and Cr of the nonresidual fraction found in contaminated soil, suggesting that the nonresidual fraction of heavy metals can readily be taken up by the pakchoi plant and also shows the highest levels of bioavailability for the pakchoi.Many studies have been conducted in recent years focused on the heavy metal remediation potential of nanomaterials in contaminated soil [26, 27]. Phosphate-based nanoparticles have been found to be one of the most effective nanomaterials for the reclamation of heavy metal contaminated soil. For instance, Liu and Zhao [28] reported that the application of iron phosphate nanoparticles in Pb-contaminated soil can effectively reduce the leachability and bioavailability of Pb2+ in soil. Moreover, Liu [29] also reported an effective reclamation of a lead-contaminated soil using synthesized apatite nanoparticles. Their experimental results clearly showed that the apatite nanoparticles solution could significantly reduce the TCLP-leachable Pb fraction in Pb-contaminated soil by 9.56% to 66.43%. Many studies have suggested that nanomaterials are superior to traditional modifications using commonly particle sizes for soil remediation due to nanomaterials having a higher reactivity and a greater ability for absorption and for its relatively easy delivery methods. Theoretically, in this study a larger amount of Pb, Zn, Cu, and Cr was able to be immobilized by nHAP, likely due to its smaller particle sizes yet larger surface area, as compared to mHAP. However, we found that mHAP was more effective than nHAP in immobilizing Pb, Zn, Cu, and Cr. Furthermore, the pH value of the soil was more greatly enhanced by mHAP. Gilbert et al. [30] and Cui et al. [18] suggested that nanomaterials can easily aggregate, leading to an alteration to their surface sorption and ability to migrate while decreasing their dissolution rates. mHAP has a larger particle size, as compared to nHAP making it much more difficult for mHAP to aggregate. Therefore, we hypothesized that the higher dissolution rate was the primary reason for the increases in the pH value and for its increased immobilization effects. Nevertheless, further studies are needed in order to verify this hypothesis.


## 4. Conclusions

The effectiveness of two different sizes of HAP particle, nanometer size particle of HAP (nHAP) and micrometer size particle of HAP (mHAP), was assessed for their ability of reducing the bioavailability of Pb, Zn, Cu, and Cr. The results showed that both mHAP and nHAP had significant effect on reducing the uptake of Pb, Zn, Cu, and Cr by pakchoi. Furthermore, both mHAP and nHAP were efficient in covering Pb, Zn, Cu, and Cr from nonresidual into residual forms. However, mHAP was superior to nHAP immobilization of Pb, Zn, Cu, and Cr in metal-contaminated soil and reducing the Pb, Zn, Cu, and Cr by pakchoi. In addition, mHAP and nHAP were both more efficient in transferring bioavailable Pb into less bioavailable form than Zn, Cu, and Cr. This may be due to the fact that more Pb was formed into insoluble pyromorphite like minerals after treated with HAP. However, in this study, it was suggested that HAP with micrometer size was more effective immobilization soil metals than nanometer size HAP, possibly due to its higher dissolution rate.



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*Source: 168418-2014-03-20.xml*