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Article

Effects of ZnO Nanoparticles and Biochar of Rice Straw and Cow Manure on Characteristics of Contaminated Soil and Sunflower Productivity, Oil Quality, and Heavy Metals Uptake

by
Mahmoud F. Seleiman
1,2,*,
Majed A. Alotaibi
1,
Bushra Ahmed Alhammad
3,
Basmah M. Alharbi
4,
Yahya Refay
1 and
Shimaa A. Badawy
5
1
Plant Production Department, College of Food and Agriculture Sciences, King Saud University, P.O. Box 2460, Riyadh 11451, Saudi Arabia
2
Department of Crop Sciences, Faculty of Agriculture, Menoufia University, Shibin El-kom 32514, Egypt
3
Biology Department, College of Science and Humanity Studies, Prince Sattam Bin Abdulaziz University, Al Kharj Box 292, Riyadh 11942, Saudi Arabia
4
Department of Biology, Faculty of Science, University of Tabuk, Tabuk 71491, Saudi Arabia
5
Agronomy Department, Faculty of Agriculture, Kafrelsheikh University, Kafr El-Sheikh 33516, Egypt
*
Author to whom correspondence should be addressed.
Agronomy 2020, 10(6), 790; https://doi.org/10.3390/agronomy10060790
Submission received: 15 May 2020 / Revised: 29 May 2020 / Accepted: 29 May 2020 / Published: 2 June 2020
(This article belongs to the Special Issue Impact of Biochar and Compost on Soil Quality and Crop Yield)
Browse Figures
Versions Notes

Abstract

:
Contaminated soils can cause a potential risk into the health of the environment and soil as well as the quality and productivity of plants. The objectives of our study were to investigate the integrative advantageous effects of foliar ZnO nanoparticles (NPs) (60 mg Zn NPs L−1), rice straw biochar (RSB; 8.0 t ha−1), cow-manure biochar (CMB, 8.0 t ha−1), and a combination thereof (50% of each) on sunflowers grown in agricultural land irrigated with polluted wastewater for the long term (≈50 years). The availability of heavy metals (HMs) in soil, HMs accumulation in whole biomass aboveground, growth, productivity, and quality characteristics of the sunflower were investigated. The combination treatment significantly minimized the availability of HMs in soil, and, consequently, substantially lessened the uptake of HMs by the sunflower, compared to treatments of ZnO NPs and control (i.e., untreated soil). The application of the combination treatment reduced the availability of Pb, Cr, Cu, and Cd in the soil by 78.6%, 115.3%, 153.3%, and 178.5% in comparison to untreated plots post-harvest, respectively. Compared to untreated plots, it also reduced the Pb, Cr, Cu, and Cd in plant biomass by 1.13, 5.19, 3.88, and 0.26 mg kg−1 DM, respectively. Furthermore, combination treatment followed by biochar as an individual application caused a significant improvement in sunflower productivity and quality in comparison to untreated soil. For instance, seed yield ha−1, 100-seed weight, and number of seeds per head obtained from the combination treatment was greater than the results obtained from the untreated plots by 42.6%, 47.0%, and 50.4%, respectively. In summary, the combined treatment of NPs and both RSB and CMB is recommended as a result of their positive influence on sunflower oil quality and yield as well as on minimizing the negative influences of HMs.

1. Introduction

Terrestrial soil contamination by heavy metals (HMs) has become a serious environmental problem worldwide as a result of anthropogenic activities [1,2,3,4,5,6,7,8,9]. Moreover, HMs and metalloids can negatively influence the ecological integrity and soil quality, and decrease the usability of agricultural soils, which, consequently, results in food insecurity. HMs and metalloids can also cause irretrievable harm to ecological systems, animals, and human health [3,7,8]. Therefore, the remediation [10] or immobilization [3] of toxic HMs in contaminated agricultural lands is considered a serious, imperative, and imperious issue. Soil contamination with toxic metalloids and HMs such as arsenic (As), lead (Pb), cadmium (Cd), chromium (Cr), nickel (Ni), copper (Cu), and zinc (Zn) has meaningfully increased in recent decades due to the sewage wastes, agricultural pesticides, chemical fertilizers, and industrial waste application [2,3,8,11]. The dispersion of toxic HMs in agricultural lands are irrigated with wastewater, and, in plant biomass or edible parts, can pose a contamination for the food chain with hazardous consequences to both animals and humans [3,8,12,13].
However, water scarcity is considered a worldwide concern that can influence socio-economic activities and threaten natural resources sustainability [6]. Treated wastewater is a necessary nonconventional water resource that can be partially used in agricultural irrigation to allow crop survival during water shortages and agricultural expansion in Egypt [14]. The Bahr El-Baqar drain is considered one of the biggest drains in the Egyptian Nile Delta. It has been receiving different wastewater resources (i.e., mainly untreated or drainage return flow from agricultural areas, poorly treated domestic, and industrial wastewater) for approximately 50 years [14]. It receives the largest quantity of wastewater yearly (1.8 billion m3) in the Egyptian Nile Delta region. The Bahr El-Baqar drain receives, daily, 4.52, 0.12, 0.06, and 0.18 million m3 of agricultural diffuse, domestic diffuse, domestic, and industrial sources, respectively. Such discharge of municipal, agricultural, and industrial wastewaters in the Bahr El-Baqar drain can easily contaminate agricultural lands with toxic metals and metalloids. Thus, traditional or nontraditional soil amendments, foliar exogenous applications, and/or plant species must be used to remove or immobilize such metals and metalloids in contaminated soil.
Biochar is a carbonaceous material created from the pyrolytic conversion of agricultural biomass (i.e., plant or animal biomass or manure) and industrial residue with limited oxygen access [4,6,15,16,17]. Recently, biochar produced from different raw materials has been recommended for agriculture and horticulture use as an organic amendment for soil because of its specific physical and chemical characterization, and its capability of adsorbing HMs and metalloids in contaminated soil [3,4,18,19]. A biochar application to agricultural soils can improve soil characteristics such as pH, bulk density, stability of the organic matter, and nutrient retention via cation adsorption [3,6]. Moreover, its application can improve the aggregate stability, water availability, microbial abundance, and mycorrhizal activity in soils [6]. It contains high silicon that can also minimize the adverse drought stress effects [6]. Burning rice straw (RS) in open air typically causes a significant contribution to heavy haze formation. Therefore, biochar produced via thermal pyrolysis of RS with limited oxygen access has been proposed to provide a promising substitute solution for using RS as a residual return to agricultural lands. Typically, agricultural land suffers from a deficiency of Si and other nutrients because of cropping and harvesting processes. Thus, Si-rich biochar such as rice straw biochar (RSB) can directly import N, P, K, and Si into this soil [6,20]. Biochar made from poultry litter feedstock [21] and/or cow-manure biochar (CMB) [22,23,24] have superior quality and nutrient status compared with that made from plant biomass or crop residues [3,6]. Cow-manure biochar (CMB) can be used as a supplement to RSB for the integrative enhancement of this combination on soil and crop productivity.
Recently, the application of nanoparticles (NPs) as foliar and/or seed priming has received significant attention due to the increment in the nutrient accumulation by plants, which enhances the capability of agronomic nutrient biofortification [25,26,27,28]. Zinc oxide (ZnO) is an instance for the NP that can be useful in this respect due to the importance of Zn as micronutrients for plants and human’s development [28,29]. Exogenous application of Zn as different forms is favored over its addition as an amendment for the soil due to its lesser bioavailability in the latter form [25,30]. The role of ZnO NPs, as an exogenous application, combined with the application of RSB or CMB has not been deeply investigated in terms of toxic metals and/or metalloids accumulating by oil crops. Agricultural lands irrigated with wastewater should also be cultivated with specific crops to prevent the entry of HMs and metalloids to the other environmental compartments. Previous studies reported that ZnO and zerovalent iron NPs caused an increase in heavy metal (i.e., Cd) accumulation by Boehmeria nivea [31] and Leucaena leucocephala [32], respectively. However, other works reported that NPs enhanced both growth characteristics and yields and lessened heavy metal accumulation in plants in comparison to a control treatment [26,27,33]. Similarly, Si-NPs lessened the toxicity of metal elements (i.e., Cr) in pea seedlings [34]. Foliar application of Fe3O4-NPs improved the wheat growth and its productivity and decreased the HMs uptake [35]. From the above, it is clear that the previous investigations have designated that NPs have different influences on heavy metal uptake due to the type and procedure of the application as well as the plant and heavy metal species involved.
Sunflower (Helianthus annuus L.) contributes 8% of the total oilseed production. The globe sunflower cultivated area and seed production were 23.1 M ha and 31.5 Mt during 2010, 25.3 M ha and 42.6 Mt during 2014, and 26.7 M ha and 52.0 Mt during 2018, respectively [36]. Sunflower seeds contain 45.5% oil and 23.8% protein [28]. The tolerance of sunflower into nutrient-poor soils, and its high seed and biomass yields make this crop a desirable feedstock for food, feed, and bioenergy production [5,25,37]. Seed oil with a high oleic acid percent are advantageous for food uses, whereas those with high linoleic acid percent are beneficial for biofuel production. Moreover, the ratio between oleic and linoleic acids is a very important characteristic for oil quality [5,38].
Therefore, the aim of our study was to investigate the effects of ZnO NPs, RSB, CMB, and/or their combination (50% for each treatment) on accumulation of HMs in whole plant biomass aboveground and on the growth, yield, and quality of sunflowers grown in soil irrigated over long periods with polluted wastewater. In addition, the effects of the different treatments on soil characteristics were studied.

2. Materials and Methods

2.1. Treatments, Design, and Plant Material of the Experiments

Two field experiments were performed in Bahr El-Baqar, East of the Nile Delta, Egypt during summer seasons in 2017 and 2018 with an objective to study the effects of plant organic amendment (8.0 t ha−1 rice straw biochar; RSB), animal organic amendment (8.0 t ha−1 cow manure biochar, CMB), inorganic NPs foliar application (60 mg Zn NPs L−1), and combinations (50% of each) on available trace elements in soil post-harvest of sunflowers (Helianthus annuus L., cv Sakha 53) grown in soil irrigated with wastewater. The plant uptake of trace elements (Cd, Cr, Pb, Zn, Fe, and Cu), oil quality (oil percent, oil yield kg ha−1, oleic acid, linoleic acid, and oleic/linoleic ratio), physiological, and productivity characteristics (total chlorophyll, proline content, plant leaf area, yield, and yield components) were also measured. The soil in the investigated area was contaminated via long-term irrigation with wastewater (i.e., for approximately 50 years). Before sowing, the biochar of animal and plant were applied into the surface and then ploughed into soil to a depth of 5–15 cm. ZnO NPs was added as foliar application at 25 and 45 days after sowing (DAS) with the rate of 60 mg Zn NPs L−1.
Biochar was made by fast pyrolysis through 500–550 °C for 20 min [6], from RS and cow-manure (CM). The analysis of CMB and RSB was pH 8.9 and 8.3, electrical conductivity (EC) 2.92 and 0.14 dS m−1, water holding capacity of 42.29% and 35.01%, carbon values at 409.3 and 465.9 g kg−1, nitrogen values at 14.32 and 9.81 g kg−1, phosphorus values at 11.42 and 1.94 and g kg−1, specific surface area of 24.14 and 22.44 m2 g−1, and potassium values of 18.34 and 20.52 g kg−1, respectively. The purity, specific surface area, particle size, and density of the ZnO NPs were 99.9%, 55 m2 g−1, 18 nm, and 5.6 g cm−3, respectively.
The experimental design was by completely block design, and the number of replications was four. The investigated area was divided into plots with a size of 25.0 m2 (5 m × 5 m) for each plot. Sunflower seeds (cv. Sakha 53) were sown on 2 June 2017 and 4 June 2018 (10 kg ha−1), and were sufficient for guaranteeing healthy germination. Seeds of the sunflower were sown in rows with a 0.6 m distance. In addition, they were sown in hills with two or three seeds per hill, and the distance between the two hills was 20 cm. Seedlings were thinned at 18 DAS, and one plant was left per hill. The preceding crop cultivated at each site was Beta vulgaris L. in both seasons.
Prior to sowing of the sunflower, calcium superphosphate (15.5% P2O5) was applied at the rate of 40 kg P2O5 ha−1 as a soil amendment. Prior to the first and second irrigations, ammonium nitrate (33.5% N) was added at the recommended rate of 80 kg ha−1. The total nitrogen amount was applied in two equal doses. Lastly, potassium fertilizer was added at the recommended rate of 54 kg K2O ha−1 directly before the first irrigation.

2.2. Water and Soil analysis

The samples from water were collected during both growing seasons and placed into plastic bottles. They were immediately acidified with nitric acid (1 mL HNO3 L−1 water) for analysis of different elements using ICP-Optical Emission Spectrometry (iCAP 6200, Thermo Fisher Scientific Inc., Cambridge, UK) as described by APHA [39]. Electrical conductivity (EC) and pH were measured using a Thermo Scientific Orion Versa Star™ advanced electrochemistry benchtop meter. The total suspended solids (TSS) as well as ammonium (NH4), nitrate (NO3), phosphate (PO4), sulfate (SO4), chloride (Cl), and molybdate (MoO4) were measured using a YSI 9300 photometer. The analysis of the water, as the mean of six sampling dates, was 0.007, 0.235, 0.016, 0.114, 0.001, 0.07, 5.2, 111.4, 16.5, 185.4, 29.3, and 134.3 mg L−1 for Cd, Pb, Cu, Mn, Zn, Fe, MoO4, SO4, PO4, NO3, NH4, and Cl, respectively.
The soil was clay loam with a sand value of 19.3%, a silt value of 34.3%, and a clay value of 46.4%, with pH 7.19, EC 1.02 dS m–1, available N at 26.49 mg kg−1, available P at 6.89 mg kg−1, and available K at 45.17 mg kg−1 (Table 1). Before sowing, the content of Cr, Pb, Cd, Ni, Cu, and Zn in the experimental area were 14.34, 3.05, 39.45, 43.81, 40.91, and 54.38 mg kg−1, respectively.

2.3. Measurements

2.3.1. Soil Analysis

Top soil samples (0–20 cm) were collected prior to sowing and post-harvest for analysis of pH (H2O; 1:2.5) and EC using the same meter mentioned above in the water analysis section.
Before starting the experiments, the total content of Cd, Zn, Cu, Cr, Ni, and Pb in the soil were analyzed as follows. To begin, 100 mg of the soil was digested in 6 mL of a mixture of HCl and HNO3 (3:1, v/v) in a Teflon tube (7 mL) for 130 min at 185 °C. The resultant solution was filtered, transferred to a 100 mL flask, and used for the metal’s measurement. The total content of HMs was measured with ICP-MS (Agilent 7500c, Agilent Technologies, CA, USA).
After harvest, subsamples of soil (250 mg from 0–20 cm depth) were taken and then well mixed to provide a single representative sample for each replication. The collected soil samples were dried in open air and ground. The soil was passed through a 2-mm sieve. The availability of HMs was extracted following Jones [40], and using the ammonium bicarbonate–diethylene triamine penta acetic acid (AB-DTPA) method. The contents of the different HMs were measured by ICP-MS (Agilent 7500c, Agilent Technologies, CA, USA).

2.3.2. Growth and Physiological Characteristics

All physiological characteristics were measured and analyzed at the flowering stage [41]. The proline content was measured in the fully expanded leaf (1.0 g) as explained by Bates et al. [42] and Seleiman et al. [6]. The absorbance was read at 520 nm using a spectrophotometer (UV-160A, Shimadzu, Japan). Lastly, proline content was measured from a calibration curve and presented as μmol proline g−1 fresh weight (FW).
The total chlorophyll was analyzed using a SPAD meter (Model: SPAD-502, Minolta Sensing Ltd, Osaka, Japan). The topmost fully expanded sunflower leaves were used for measuring total chlorophyll. We measured the total chlorophyll content from 10 different plants within each replicate.
Moreover, six plants were randomly harvested from each replication at the flowering stage to measure the leaves area per plant using Portable Leaf Area Meter (LI-3000C, LI-COR Inc., Lincoln, NE, USA). Furthermore, the sunflower plant height from the soil surface to the plant top were recorded. Additionally, the diameter of the sunflower stem at 30 cm from the soil surface was measured.

2.3.3. Yield and Yield Components

On September 14, 2017 and September 12, 2018, sunflower plants with an area of 2 m2 were manually harvested for measuring yield and related characteristics. Head diameter (cm), head weight (g), and number of seeds per head were recorded from five sunflower plants, which were chosen randomly and, subsequently, averaged. Seed index (100-seed weight, g) was measured by counting 100 seeds from the collected heads by the random method. Seed yield of sunflowers (kg ha−1) was measured as follows. The heads of collected plants from the inner ridges (two m2) in each plot were kept for two weeks after harvest until being completely air dried. Then, seeds were separated from heads to measure seed yield ha−1.

2.3.4. Plant Uptake for Trace Elements and Seed Quality at Harvest

To analyze the toxic metals, the oven-dried biomass plant samples were ground. A subsample of 0.3 g was weighed from each replication and inserted in a Teflon tube with HNO3− for digesting by microwave heating. The digested sunflower samples were filtered, and then analyzed via ICP-Optical Emission Spectrometry (iCAP 6200, Thermo Fisher Scientific Inc., Cambridge, UK) as explained by Seleiman et al. [1].
The sunflower seeds were oven dried for 4 h at 40 °C, and, afterward, were ground using a Waring Blender (Waring Product Division, New Hartford, CT, USA). The percentage of sunflower oil seeds was analyzed by using the petroleum ether extraction technique with a Soxhlet meter [43]. The oil extract of different samples was evaporated via distillation by using a rotary evaporator at 35 °C until the solvent was completely removed. Lastly, the crude extract of oil was weighed to get the seed oil percent.
The oil yield (kg ha−1) was calculated as follows.
Oil   yield   ( kg   ha − 1 ) = O i l   s e e d   % × s e e d   y i e l d   ( k g   h a − 1 ) .
For analyzing the fatty acids such as oleic and linoleic, a 2-g aliquot of seed oil was moved to a screw-capped vial containing 0.3 mL methanol:sodium methylate (28.5:1.5 w/w) and incubated at 90 °C for 2 h to allow the methylation of the fatty acids. The composition of oleic and linoleic acids in the oil was analyzed as explained by Rotunno et al. [44] and Seleiman et al. [6]. The oleic/linoleic ratio was calculated as follows.
l e i c / l i n o l e i c   r a t i o = Oleic   content Linoleic   content

2.4. Statistical Analysis

Results obtained from the effects of investigated treatments (Zn NP, RSB, CMB, and their combination) on soil analysis after the experiment, sunflower oil quality, plant elemental analysis, and productivity characteristics were subjected to analysis of variance (ANOVA) using PASW statistics 21.0 (IBM Inc., Chicago, IL, USA). Combined statistical analysis over the two growing seasons for some investigated measurements was used. Treatment means were compared using Tukey’s multiple range test at a significant difference of p ≤ 0.05. Least significant difference was also calculated. Simple correlation coefficient among different measurements such as metals in soil postharvest, metals in sunflower, yield, and quality traits was done.

3. Results

3.1. Integrative Effects of NPs, CMB, and RSB on Contaminated Soil Characteristics

Application of RSB, CMB, and a combination into soil enhanced organic soil carbon levels (Figure 1). However, these applications did not cause a significant increase in the soil pH and EC when compared to the untreated soil. On the other hand, the application of a combination treatment (i.e., RSB + CMB + ZnO NPs) after that application of CMB and RSB caused the lowest availability of HMs (Cr, Cd, Cu, and Pb) and the highest availability of Zn and Fe in the soil after sunflower harvest. This was compared to ZnO NPs treatment and untreated soil (Figure 1). Compared to the untreated plots post-harvest, the combination of different treatments reduced the availability of Pb, Cr, Cu, Cd, and Ni in the soil by 78.6%, 115.3%, 153.3%, 178.5%, and 193.7%, respectively.

3.2. Integrative effects of NPs, CMB, and RSB on HMs Accumulation in Biomass of Sunflowers Grown in Contaminated Soil

The application of both organic amendments (i.e., CMB and RSB) and inorganic NPs (Zn NPs) in the current investigation significantly lessened the contents of Cd, Cu, Cr, and Pb in the whole sunflower biomass, and significantly enhanced the Zn and Fe when compared with the plants grown in the control (Figure 2). The lowest Cd, Cr, Cu, and Pb contents in the whole plant biomass were found when a combination treatment was added. This was followed by the individual CMB, RSB, and/or Zn NPs application being compared with the data obtained from sunflowers grown in the untreated plots (Figure 2). Compared to the control treatment, the combination treatment (i.e., CMB + RSB + Zn NPs) reduced Cd, Cr, Cu, and Pb in plant biomass by 0.26, 5.19, 3.88, and 1.13 mg kg−1 DM, respectively. However, the highest Zn content (25.1 mg kg−1 DM) in the plant biomass was obtained when the soil was incorporated with a combination treatment, which was followed by CMB and Zn NPs compared with RSB and control treatments. The highest Fe content (75.4 mg kg−1 DM) in the plant biomass was obtained when the soil was treated with a combination treatment that was followed by CMB and RSB when compared to Zn NPs and control treatments (Figure 2). The highest content of trace elements in the sunflower biomass was Fe followed by Zn, Cu, Cr, and Pb while the lowest element was Cd (Figure 2).

3.3. Integrative Effects of NPs, CMB, and RSB on Growth, Physiological, And Yield Properties Of Sunflowers Grown In Contaminated Soil

The application of NPs (i.e., Zn NPs), CMB, RSB, and their combination enhanced growth, physiological, and yield characteristics of sunflowers grown in contaminated soil compared with untreated soil (Table 2 and Figure 3 and Figure 4). The combination treatment (Zn NPs + RSB + CMB) resulted in the highest plants, widest stem, widest head diameters, greatest number of seeds per head, and seed yield ha−1. This was followed by a single application of CMB, RSB, and Zn NPs when compared to the untreated soil. The seed yield ha−1, 100-seed weight, number of seeds per head, and head diameter obtained from the combination treatment was greater than the results obtained from the untreated soil by 42.6%, 47.0%, 50.4%, and 52.4%, respectively (Table 2). Compared to the untreated soil, the application of a single CMB and RSB increased the seed yield ha−1 by 27.5% and 21.8%, 100-seed weight by 41.3% and 25.6%, number of seeds per head by 40.0% and 26.6%, and head diameter by 33.1% and 26.9%, respectively (Table 2). The foliar application with Zn NPs increased the seed yield ha−1, 100-seed weight, number of seeds per head, and head diameter by 19.2%, 6.7%, 9.2%, and 5.7% when compared to the results obtained from the untreated soil, respectively.
The total chlorophyll content was increased gradually from 25 to 45 DAS, and was then decreased (Figure 3). The highest sunflower chlorophyll content at all sampling dates was obtained when the combination treatment was applied, compared to untreated soil. This was followed by applications of CMB, RSB, and Zn NPs (Figure 3). Compared to the untreated soil, the application of a combination treatment (i.e., CMB + RSB + Zn NPs) increased the total chlorophyll content by 26.6%, 29.9%, 27.4%, and 35.6% at 25, 45, 65, and 85 DAS, respectively (Figure 3).
Effects of NPs, RSB, CMB, and their combination on proline content and total leaf area of sunflowers grown in long-term contaminated soil are illustrated in Figure 4. The greatest leaf area per plant and proline content of sunflower grown in polluted soil was obtained from plots given the combination treatment. This was followed by CMB, RSB, and Zn-NPs compared to the untreated soil (Figure 4). The proline content obtained from sunflowers grown with a combination treatment, and single application of CMB, RSB, and Zn NPs was greater by 29.6%, 30.9%, 16.1%, and 17.6% than sunflowers grown in untreated soil, respectively (Figure 4).

3.4. Integrative Effects of NPs, CMB, and RSB on Oil Quality Characteristics of Sunflowers Grown in Contaminated Soil

The application of different soil amendments (i.e., CMB and RSB) and exogenous Zn NPs application increased the sunflower oil percentage and yield, oleic acid, and oleic/linoleic acids ratio compared to these factors in sunflowers grown in untreated soil (Table 3). The oil percentage was greater by 25.1% and 13.3% in seeds of sunflower grown on soil treated with a combination and CMB treatments. This was compared with those found in sunflowers grown in control treatment (Table 3). Compared with untreated soil, the oil yield increased by 537, 305, 202, and 214 kg ha−1 with a combination treatment and when CMB, RSB, and Zn NPs was applied into the soil, respectively. The application of a combination treatment (i.e., CMB + RSB + Zn NPs) increased the oleic acid by 12.4.0% and oleic/linoleic ratio by 316.7%. It reduced the linoleic acid by 252.5% when compared to the results obtained from the plants grown in the untreated plots (Table 3).

3.5. Simple Correlation Coefficient Aming Different Traits over All Treatments

The results of a simple correlation coefficient among most investigated traits, such as heavy metals in soil post-harvest and metals uptake in sunflower, growth, yield, and quality traits, are presented in Table 4. Seed yield ha−1 and oleic acid in sunflower oil were significantly and positively correlated with Zn availability in soil and sunflower plants post-harvest, proline, leaf area per plant, and oil percentage. Reversely, they were negatively and significantly correlated with the Cu, Cr, and Cd in soil and sunflower plants post-harvest as well as with linoleic acid (Table 4). Conversely, correlation coefficient was non-significant between oleic acid with Zn and Cu in soil post-harvest or with an oil percentage.

4. Discussion

4.1. Irrigation Water Analysis

In the investigated area, the HMs concentration in the Bahr El-Baqar Drain water were under the maximum limited values for field crops irrigation. Considering the crop tolerance level, the salinity range for crop irrigation water is 0–3 dS m−1 [45] while it was 1.5 dS m−1 in the irrigation water used in our investigation. In our study, the content of Mn, Cu, Fe, Zn, Pb, and Cd in the water of irrigation were 0.114, 0.016, 0.07, 0.001, 0.235, and 0.007 mg L−1; while the recommended maximum values for these elements were 5, 2, 0.2, 0.2, 0.5, and 0.01 mg L−1, respectively [45]. The high value of molybdenum (5.2 mg L−1) in the irrigation water might be a result of the industrial wastewater, where molybdenum is encompassed in numerous chemicals such as catalysts, corrosion inhibitors, and pigments [46].

4.2. Integrative Effects of NPs, Plant, and Animal Biochar on Soil Trace Elements, pH, EC, and Organic Matter Postharvest

The pH in the soil mixed with biochar or plots treated with NPs at harvest were comparable with those of the control treatment (Figure 1). Such results show that both biochars and/or NPs fertilizers had no further liming impact on the treated soil, which can be a critical issue in alkaline soils. Regarding the soil EC, biochar application derived from CM or RS resulted in a non-significant increase in the soil EC when compared to the untreated soil or plots treated with ZnO NPs (Figure 1). This was a result of the high ash content of animal and plant biochar. However, the ECs were obtained from our study due to the different treatments being less than the recommended threshold for the majority of crops including sunflowers, and less than the ECs of saline soils (≥2000 μS cm−1) [47]. The increment of the soil EC in plots treated with biochar can be linked to the release of fused-ring aromatic structures from both biochars.
The application of a combination treatment, CMB, RSB, and ZnO NPs into the contaminated soil significantly reduced the availability of HMs in the soil post-harvest compared to the results obtained from the untreated soil or plots treated with ZnO NPs (Figure 1). The possible mechanisms of toxic metals’ mobility and bioavailability in different soils, as a result of biochar application, include complexation, ion exchange, electrostatic attraction, and precipitation [4]. Biochar made from animal or crop residues can adsorb HMs and metalloids by forming a surface complexation [48]. The functional groups such as -OH, -COOH, -C=O-, and C=N in biochar provide binding sites for toxic metals to form complexes, which can increase the specific adsorption of toxic metals [49]. The functional groups in biochar have demonstrated an immobilization of 38%–42% from total sorbed Pb (II) in acid solutions compared with untreated ones [50]. The inorganic ions present in biochar, such as Si, S, and Cl, can complex metals such as Cd by reducing their mobility in the soil [49]. Moreover, the elements presented in biochar can precipitate with different HMs to form insoluble precipitates [22,23]. For example, the application of phosphorus-rich biochar into contaminated soil can lessen the availability and leaching of Cd and Pb when compared to phosphorus-low biochar [51]. Conversely, the soil treated with a combination treatment, followed by CMB and RSB, contained greater Fe and Zn post-harvest than the untreated soil (Figure 1). This could be due to the ability of biochar to increase the capacity of the soils for adsorbing plant nutrients [3,6,52].
The application of biochar into contaminated soil can mitigate the risks of HMs by incrementing the soil pH [4] and/or number of cation exchange sites on the biochar surfaces [3,53]. Consequently, this could increase the hydrolysis of toxic metals and enhance their adsorption via the soil and accelerate the transformation of the oxidizable as well as residual fractions of the HMs [54]. Conversely, the released mineral elements could form mineral phases on the biochar surfaces and adsorb the HMs and metalloids from the soil solution [55]. For example, the phosphorus was enhanced in the soil solution due to an increased application of biochar, which causes heavy metal retention because of stable phosphate mineral formation [22]. In addition, oxides of Si, Ca, and Mn in biochar can be partially reduced and postulated high-energy sorption sites for heavy metal cations in the soils [55]. Moreover, biochar can release dissolved organic carbon (OC). Consequently, its application can enhance soil organic matter (Figure 1), which could, therefore, lessen the toxic metal mobility in the soil solution as a result of the complexation between the toxic metals and oxygen-containing functional groups presented in the biochar [56]. According to the biochar production cost and economic value, biochar derived from RS or CM can be used in heavy metal contaminated soils because such feedstock is abundant and low cost.

4.3. Integrative Effects of NPs, Plant, and Animal Biochar on Heavy Metal Accumulation in the Biomass of Sunflowers Grown in Contaminated Soil

The application of a combination treatment (i.e., RSB, CMB, and ZnO NPs) followed by a single application of each treatment into soil irrigated for a long period with wastewater significantly lessened the content of the toxic metals such as Cd, Cr, Cu, and Pb in the plant biomass when compared to the untreated soil (Figure 2).This can be due to the decrease in the mobility and/or bioavailability of the toxic metals in the soils (Figure 1). Biochar has high cation-exchange capacity (CECs), which can release cations such as Ca (II) and Mg (II). Such cations can exchange with the heavy metal ions on the biochar surfaces [53]. Moreover, the application of NPs such as ZnO can minimize the negative influence of the toxic metals on the sunflower growth and productivity when compared with the untreated plants. Hussain et al. [25] found that the exogenous and soil application of ZnO NPs improved photosynthesis, growth, and yield characteristics of wheat grown in soil polluted with Cd. At the same time, Cd and Zn content in different wheat parts were reduced and increased, respectively. They also reported that Cd content in the wheat grains was reduced by 30%–77%, and 16%–78% with exogenous and soil amendment of ZnO NPs when compared to the control, respectively.
The current investigation revealed that the combination treatment (CMB + RSB + ZnO NPs) followed by a single application of CMB and/or RSB was an effective application in terms of lessening the uptake of toxic metals and metalloids by the sunflowers (Figure 2). Biochar application into the contaminated soil can minimize the toxic metal uptake by the plants by depressing the heavy metal availability through the adsorption process and pH-driven fixation reactions [24,57,58]. In addition, biochar can influence the heavy metal detoxification in the plants by modifying soil pH, toxic metals immobilization, and improvement of chemical, physical, and biological soil characteristics. Moreover, biochar, as a soil amendment, can enhance the negative charge. Consequently, this can cause a suitable rhizosphere between the cations and soil particles [57].
The application of biochar in the current investigation had a low effect on the Zn content in the plant biomass. However, it significantly reduced the content of other toxic metals such as Pb, Cd, Cu, and Cr (Figure 2). This could be because of the variation in the mobility of specific HMs. The plant biomass in our investigation contained higher Pb than Cd under different treatments (Figure 2). HMs can compete with each other for active exchange surfaces in multi-metal contaminated soils. Hence, one specific heavy metal can become more mobile than another. Moreover, the low content of toxic metals obtained from the plants grown in plots treated with biochar, when compared with the untreated plots, might be due to the precipitation of these toxic metals in the root tissue of plants [24]

4.4. Effect of Different Treatments on Growth, Yield, and Oil Quality Characteristics of Sunflowers

The effects of CMB, RSB, ZnO NP, and their combination on the growth, physiological, yield, and quality characteristics of sunflowers were positively significant at p ≤ 0.01. In addition, those treatments significantly enhanced the sunflower tolerance against heavy metal stress. Plant growth characteristics (i.e., plant height and stem diameter), physiological characteristics (i.e., total chlorophyll, proline content, and leaf area plant−1), yield, and related characteristics (i.e., head diameter, number of seeds per head, 100-seed weight, seed yield ha−1) are considered the major visual observations under abiotic and biotic stresses. The obtained improvements in such characteristics might be attributed to the mixed effects of soil nutrients and moisture availability induced by both biochars. The high porosity of carbonaceous material biochar might increase the surface area of the treated soil. Consequently, there was increased surface binding of the nutrient cations and anions [20,59]. Application of biochars to soil can work as adsorbers to lessen the nitrogen from leaching, which can increase N-use efficiency [60]. Moreover, the porous structure of biochar can improve the absorbance of water [61]. However, the low values of growth and yield characteristics obtained from plants (Table 2 and Figure 3 and Figure 4) could be linked with the high toxic metals availability in the soil postharvest (Figure 1, Table 4) and high toxic metals uptake in the sunflower plants (Figure 2, Table 4). Such causes can reduce the total chlorophyll and proline contents in the sunflower leaves (Figure 3 and Figure 4).
Different studies have illustrated that HMs, in particular Cd and Pb, initiated stress in plants and lessened the plant growth and its biomass [1,2,3,26,62]. In the current study, biochar or ZnO NP application significantly improved the growth, yield, and quality of the sunflowers compared to the untreated plants. However, the combination application of CMB, RSB, and ZnO NPs could have dual effects in improving the sunflower growth and productivity. This could be due to the positive influence of biochar (i.e., CMB and RSB) in terms of reducing the soluble HMs such as Cd, Pb, and Cr in the soil (Figure 1). Consequently, the HMs decreased in the sunflower biomass (Figure 2). This could be the reason for the enhanced growth, physiology, and productivity of the plants grown in the soil treated with the combination treatment (Table 2, Figure 3 and Figure 4). Biochar has the ability to immobilize HMs and metalloids in the soil due to metal speciation and soil pH [3,19]. The significant improvement in proline, total chlorophyll content, and leaf area per plant as a result of the combined CMB, RSB, and ZnO NPs treatment in the current study could be due to minimizing of the oxidative stress and enhancing of the enzyme activities in the plant [26,27]. ZnO NPs can be considered slow-release for Zn fertilization [53]. These NPs can avoid the sudden absorption of Zn by plants, as the high uptake of Zn can cause toxicity in plants. Therefore, foliar application of nutrients could be considered an efficient agronomic strategy for enhancing the nutrients in plants. The optimal content of Zn in the soil or plants can interfere with HMs and metalloids such as Cd. Thus, it can lessen the accumulation of HMs by plants because of the antagonistic effects for these metals on each other [63].
Recent investigation has reported that crop biochar contains biogenic silica and can rapidly release bioavailable silicon to enhance plant growth and its biomass as well as promote the biological silicon cycle in the soil [6,64]. Biochar as a soil amendment has the ability to store nitrogen by increasing NH3− and NH4+ retention. In addition, it can enhance the nitrogen bacteria, which can directly increment the soil productivity [65].
A combination treatment followed by an individual treatment of CMB resulted in the highest oil percent and yield ha−1 compared to RSB, ZnO NPs, and untreated plants (Table 3). Moreover, a combination treatment followed by both animal and plant biochar significantly increased the oleic acid and oleic/linoleic acid ratio when compared to the ZnO NPs or untreated plants (Table 3). This could be because of the beneficial integrative effects of the combination treatments in terms of reducing the stress physiology of HMs on the plant growth and productivity. The high quality of sunflower oil (i.e., 91.2% oleic acid and 2.4% linoleic acid, 41.1% oil percent) obtained from the plants grown with a combination treatment when compared to other treatments could be a beneficial product for human health. The high density of the oleic acid in oil is important since humans cannot synthesize such a fatty acid [6,66].

5. Conclusions

The combination treatment, which included CMB, RSB, and ZnO NPs, significantly improved the soil characteristics in terms of reducing toxic metals availability, lessened the uptake of toxic metals in the biomass, enhanced growth and physiological characteristics, increased yield, and improved quality of the sunflowers grown in soil irrigated with long-term wastewater when compared to each individual treatment. For instance, seed yield ha−1, 100-seed weight, and number of seeds per head obtained from the combination treatment was greater than the results obtained from the untreated plots by 42.6%, 47.0%, and 50.4%, respectively. Furthermore, the application of the combination treatment reduced the availability of Pb, Cr, Cu, Cd, in the soil by 78.6%, 115.3%, 153.3%, and 178.5% in comparison to untreated plots post-harvest, respectively. Compared to untreated plots, it also reduced the Pb, Cr, Cu, and Cd in plant biomass by 1.13, 5.19, 3.88, and 0.26 mg kg−1 DM, respectively. In conclusion, the combined application of NPs and both animal and plant biochar is recommended due to the positive influence on sunflower yield and quality, and due to alleviating and minimizing the negative influence of HMs and metalloids in semi-arid regions. Further research is needed to investigate the residual effect of NPs and biochar over the long-term.

Author Contributions

Conceptualization: M.F.S. Data curation: M.F.S. and S.A.B. Formal analysis: M.F.S., M.A.A., B.A.A., B.M.A., and S.A.B. Investigation: M.F.S., Y.R., M.A.A., B.M.A., and S.A.B. Methodology: M.F.S., M.A.A., B.A.A., B.M.A., and S.A.B. Resources: M.F.S., M.A.A., Y.R., and S.A.B. Software: M.F.S., M.A.A., B.A.A., B.M.A., Y.R., and S.A.B. Writing—original draft: M.F.S., M.A.A., B.A.A., B.M.A., and S.A.B. Writing—review and editing: M.F.S., M.A.A., B.A.A., B.M.A., Y.R., and S.A.B. All authors have read and agreed to the published version of the manuscript.

Funding

The Deanship of Scientific Research at King Saud University through the research group number RG-1441-323 funded this study.

Acknowledgments

The authors extend their appreciation to the Deanship of Scientific Research at King Saud University for funding this work through research group number RG-1441-323. Furthermore, Researchers Support & Services Unit (RSSU) is acknowledged for technical support in terms of language editing and plagiarism verification.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Seleiman, M.F.; Santanen, A.; Stoddard, F.L.; Mäkelä, P. Feedstock quality and growth of bioenergy crops fertilized with sewage sludge. Chemosphere 2012, 89, 1211–1217. [Google Scholar] [CrossRef] [PubMed]
  2. Seleiman, M.F.; Santanen, A.; Jaakkola, S.; Ekholm, P.; Hartikainen, H.; Stoddard, F.L.; Mäkelä, P.S. Biomass yield and quality of bioenergy crops grown with synthetic and organic fertilizers. Biomass Bioenergy 2013, 59, 477–485. [Google Scholar] [CrossRef]
  3. Seleiman, M.F.; Kheir, A.M. Maize productivity, heavy metals uptake and their availability in contaminated clay and sandy alkaline soils as affected by inorganic and organic amendments. Chemosphere 2018, 204, 514–522. [Google Scholar] [CrossRef] [PubMed]
  4. He, L.; Zhong, H.; Liu, G.; Dai, Z.; Brookes, P.C.; Xu, J. Remediation of heavy metal contaminated soils by biochar: Mechanisms, potential risks and applications in China. Environ. Pollut. 2019, 252, 846–855. [Google Scholar] [CrossRef]
  5. Saleem, M.H.; Ali, S.; Seleiman, M.F.; Rizwan, M.; Rehman, M.; Aisha Akram, N.; Liu, L.; Alotaibi, M.; Al-Ashkar, I.; Mubushar, M. Assessing the correlations between cifferent traits in copper-sensitive and copper-resistant varieties of Jute (Corchorus capsularis L.). Plants 2019, 8, 545. [Google Scholar] [CrossRef] [Green Version]
  6. Seleiman, M.F.; Refay, Y.; Al-Suhaibani, N.; Al-Ashkar, I.; El-Hendawy, S.; Hafez, E.M. Integrative effects of rice-straw biochar and silicon on oil and seed quality, yield and physiological traits of Helianthus annuus L. grown under water deficit stress. Agronomy 2019, 9, 637. [Google Scholar] [CrossRef] [Green Version]
  7. Seleiman, M.F.; Ali, S.; Refay, Y.; Rizwan, M.; Alhammad, B.A.; El-Hendawy, S.E. Chromium resistant microbes and melatonin reduced Cr uptake and toxicity, improved physio-biochemical traits and yield of wheat in contaminated soil. Chemosphere 2020, 250, 126239. [Google Scholar] [CrossRef]
  8. Seleiman, M.F.; Santanen, A.; Mäkelä, P.S. Recycling sludge on cropland as fertilizer–Advantages and risks. Resour. Conserv. Recycl. 2020, 155, 104647. [Google Scholar] [CrossRef]
  9. Shahid, M.J.; Ali, S.; Shabir, G.; Siddique, M.; Rizwan, M.; Seleiman, M.F.; Afzal, M. Comparing the performance of four macrophytes in bacterial assisted floating treatment wetlands for the removal of trace metals (Fe, Mn, Ni, Pb, and Cr) from polluted river water. Chemosphere 2020, 243, 125353. [Google Scholar] [CrossRef]
  10. Xia, Y.; Liu, H.; Guo, Y.; Liu, Z.; Jiao, W. Immobilization of heavy metals in contaminated soils by modified hydrochar: Efficiency, risk assessment and potential mechanisms. Sci. Total Environ. 2019, 685, 1201–1208. [Google Scholar] [CrossRef]
  11. Morgan, R. Soil, Heavy Metals, and Human Health. In Soils and Human Health; CRC Press: Boca Raton, LA, USA, 2013; pp. 74–97. [Google Scholar]
  12. Jolly, Y.N.; Islam, A.; Akbar, S. Transfer of metals from soil to vegetables and possible health risk assessment. SpringerPlus 2013, 2, 385. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  13. Seleiman, M.F.; Selim, S.; Jaakkola, S.; Mäkelä, P.S. Chemical composition and in vitro digestibility of whole-crop maize fertilized with synthetic fertilizer or digestate and harvested at two maturity stages in Boreal growing conditions. Agric. Food Sci. 2017, 26, 47–55. [Google Scholar] [CrossRef] [Green Version]
  14. Elbana, T.A.; Bakr, N.; George, B.; Elbana, M.J.W. Assessment of marginal quality water for sustainable irrigation management: Case study of Bahr El-Baqar area, Egypt. Water Air Soil Pollut. 2017, 228, 211–217. [Google Scholar] [CrossRef]
  15. Wu, W.; Yang, M.; Feng, Q.; McGrouther, K.; Wang, H.; Lu, H.; Chen, Y. Chemical characterization of rice straw-derived biochar for soil amendment. Biomass Bioenergy 2012, 47, 268–276. [Google Scholar] [CrossRef]
  16. Lehmann, J.; Joseph, S. Biochar for Environmental Management: Science, Technology and Implementation, 2nd ed.; Routledge: London, UK; New York, NY, USA, 2015. [Google Scholar]
  17. Al-Wabel, M.I.; Hussain, Q.; Usman, A.R.; Ahmad, M.; Abduljabbar, A.; Sallam, A.S.; Ok, Y.S. Impact of biochar properties on soil conditions and agricultural sustainability: A review. Land Degrad. Dev. 2018, 29, 2124–2161. [Google Scholar] [CrossRef]
  18. Meng, J.; Tao, M.; Wang, L.; Liu, X.; Xu, J. Changes in heavy metal bioavailability and speciation from a Pb-Zn mining soil amended with biochars from co-pyrolysis of rice straw and swine manure. Sci. Total Environ. 2018, 633, 300–307. [Google Scholar] [CrossRef]
  19. O’Connor, D.; Peng, T.; Zhang, J.; Tsang, D.C.; Alessi, D.S.; Shen, Z.; Bolan, N.S.; Hou, D. Biochar application for the remediation of heavy metal polluted land: A review of in situ field trials. Sci. Total Environ. 2018, 619, 815–826. [Google Scholar]
  20. Chan, K.Y.; Xu, Z. Biochar: Nutrient properties and their enhancement. In Biochar for Environmental Management; Routledge: Abingdon-on-Thames, UK, 2012; pp. 99–116. [Google Scholar]
  21. Sikder, S.; Joardar, J. Biochar production from poultry litter as management approach and effects on plant growth. Int. J. Recycl. Org. Waste Agric. 2019, 8, 47–58. [Google Scholar] [CrossRef] [Green Version]
  22. Cao, X.; Ma, L.; Gao, B.; Harris, W. Dairy-manure derived biochar effectively sorbs lead and atrazine. Environ. Sci. Technol. 2009, 43, 3285–3291. [Google Scholar] [CrossRef]
  23. Cao, X.; Harris, W. Properties of dairy-manure-derived biochar pertinent to its potential use in remediation. Bioresour. Technol. 2010, 101, 5222–5228. [Google Scholar] [CrossRef]
  24. Eissa, M.A. Effect of cow manure biochar on heavy metals uptake and translocation by zucchini (Cucurbita pepo L). Arab. J. Geosci. 2019, 12, 48. [Google Scholar] [CrossRef]
  25. Hussain, A.; Ali, S.; Rizwan, M.; ur Rehman, M.Z.; Javed, M.R.; Imran, M.; Chatha, S.A.S.; Nazir, R. Zinc oxide nanoparticles alter the wheat physiological response and reduce the cadmium uptake by plants. Environ. Pollut. 2018, 242, 1518–1526. [Google Scholar] [CrossRef] [PubMed]
  26. Rizwan, M.; Ali, S.; ur Rehman, M.Z.; Adrees, M.; Arshad, M.; Qayyum, M.F.; Ali, L.; Hussain, A.; Chatha, S.A.S.; Imran, M. Alleviation of cadmium accumulation in maize (Zea mays L.) by foliar spray of zinc oxide nanoparticles and biochar to contaminated soil. Environ. Pollut. 2019, 248, 358–367. [Google Scholar] [CrossRef] [PubMed]
  27. Rizwan, M.; Ali, S.; Ali, B.; Adrees, M.; Arshad, M.; Hussain, A.; ur Rehman, M.Z.; Waris, A.A. Zinc and iron oxide nanoparticles improved the plant growth and reduced the oxidative stress and cadmium concentration in wheat. Chemosphere 2019, 214, 269–277. [Google Scholar] [CrossRef]
  28. Seleiman, M.F. Use of Plant Nutrients in Improving Abiotic Stress Tolerance in Wheat. In Wheat Production in Changing Environments; Springer: Berlin/Heidelberg, Germany, 2019; pp. 481–495. [Google Scholar]
  29. Cakmak, I.; Kutman, U. Agronomic biofortification of cereals with zinc: A review. Eur. J. Soil Sci. 2018, 69, 172–180. [Google Scholar] [CrossRef] [Green Version]
  30. Javed, H.; Naeem, A.; Rengel, Z.; Dahlawi, S. Timing of foliar Zn application plays a vital role in minimizing Cd accumulation in wheat. Environ. Sci. Pollut. Res. 2016, 23, 16432–16439. [Google Scholar]
  31. Gong, X.; Huang, D.; Liu, Y.; Zeng, G.; Wang, R.; Wan, J.; Zhang, C.; Cheng, M.; Qin, X.; Xue, W. Stabilized nanoscale zerovalent iron mediated cadmium accumulation and oxidative damage of Boehmeria nivea (L.) Gaudich cultivated in cadmium contaminated sediments. Environ. Sci. Technol. 2017, 51, 11308–11316. [Google Scholar] [CrossRef]
  32. Venkatachalam, P.; Jayaraj, M.; Manikandan, R.; Geetha, N.; Rene, E.R.; Sharma, N.; Sahi, S.J.P.P. Biochemistry. Zinc oxide nanoparticles (ZnONPs) alleviate heavy metal-induced toxicity in Leucaena leucocephala seedlings: A physiochemical analysis. Plant Physiol. Biochem. 2017, 110, 59–69. [Google Scholar] [CrossRef]
  33. Wang, M.; Chen, L.; Chen, S.; Ma, Y. Alleviation of cadmium-induced root growth inhibition in crop seedlings by nanoparticles. Ecotoxicol. Environ. Saf. 2012, 79, 48–54. [Google Scholar] [CrossRef]
  34. Tripathi, D.K.; Singh, V.P.; Prasad, S.M.; Chauhan, D.K.; Dubey, N.K. Silicon nanoparticles (SiNp) alleviate chromium (VI) phytotoxicity in Pisum sativum (L.) seedlings. Plant Physiol. Biochem. 2015, 96, 189–198. [Google Scholar] [CrossRef]
  35. Konate, A.; He, X.; Zhang, Z.; Ma, Y.; Zhang, P.; Alugongo, G.M.; Rui, Y. Magnetic (Fe3O4) nanoparticles reduce heavy metals uptake and mitigate their toxicity in wheat seedling. Sustainability 2017, 9, 790. [Google Scholar] [CrossRef] [Green Version]
  36. FAOSTAT. Food and Agriculture Organization of the United Nations Statistics Division. 2020. Available online: http://faostat.fao.org/site/567/DesktopDefault.aspx (accessed on 14 January 2020).
  37. Harris, T.M.; Hottle, T.A.; Soratana, K.; Klane, J.; Landis, A.E. Life cycle assessment of sunflower cultivation on abandoned mine land for biodiesel production. J. Clean. Prod. 2016, 112, 182–195. [Google Scholar] [CrossRef]
  38. Ghobadi, M.; Taherabadi, S.; Ghobadi, M.-E.; Mohammadi, G.-R.; Jalali-Honarmand, S. Antioxidant capacity, photosynthetic characteristics and water relations of sunflower (Helianthus annuus L.) cultivars in response to drought stress. Ind. Crop. Prod. 2013, 50, 29–38. [Google Scholar] [CrossRef]
  39. APHA. Standard Methods for the Examination of Water and Waste Water; American Public Health Association: Washington, DC, USA, 1999; p. 541. [Google Scholar]
  40. Jones, J.R. Laboratory Guide for Conducting Soil Tests and Plant Analysis; CRC Press: Boca Raton, LA, USA, 2001. [Google Scholar]
  41. Meier, U.B.-M. Growth Stages of Mono-and Dicotyledonous Plants, 2nd ed.; Federal Biological Research Centre for Agriculture and Forestry: Berlin, Germany, 2001. [Google Scholar]
  42. Bates, L.S.; Waldren, R.P.; Teare, I. Rapid determination of free proline for water-stress studies. Plant Soil 1973, 39, 205–207. [Google Scholar] [CrossRef]
  43. Pomeranz, Y.; Clifton, E. Food Analysis: Theory and Practice, 3rd ed.; Kluwer Academic Publisher: San Diego, CA, USA, 1994. [Google Scholar]
  44. Rotunno, T.; Sevi, A.; Di Caterina, R.; Muscio, A. Effects of graded levels of dietary rumen-protected fat on milk characteristics of Comisana ewes. Small Rumin. Res. 1998, 30, 137–145. [Google Scholar] [CrossRef]
  45. Ayers, R.S.; Westcot, D.W. Water quality for agriculture. Irrigation and drainage paper 29 (Rev.1); Food and Agriculture Organization of the United Nations: Rome, Italy, 1994; Available online: http://www.fao.org/3/T0234E/T0234E00.htm (accessed on 10 April 2020).
  46. Alloway, B.J. Molybdenum. In Heavy Metals in Soils: Trace Metals and Metalloids in Soils and their Bioavailability; Alloway, B.J., Ed.; Environ. Pollut.; Springer Science & Business Media: Dordrecht, The Netherlands, 2013; pp. 528–534. [Google Scholar]
  47. Soil Survey Division Staff. Soil Survey Manual. U.S. Deptment of Agriculture Handbook No. 18; U.S. Government Printing Office: Washington, DC, USA, 1993.
  48. Xu, X.; Zhao, Y.; Sima, J.; Zhao, L.; Mašek, O.; Cao, X. Indispensable role of biochar-inherent mineral constituents in its environmental applications: A review. Bioresour. Technol. 2017, 241, 887–899. [Google Scholar] [CrossRef] [Green Version]
  49. Tan, Z.; Wang, Y.; Zhang, L.; Huang, Q. Study of the mechanism of remediation of Cd-contaminated soil by novel biochars. Environ. Sci. Pollut. Res. 2017, 24, 24844–24855. [Google Scholar] [CrossRef]
  50. Lu, H.; Zhang, W.; Yang, Y.; Huang, X.; Wang, S.; Qiu, R. Relative distribution of Pb2+ sorption mechanisms by sludge-derived biochar. Water Res. 2012, 46, 854–862. [Google Scholar] [CrossRef]
  51. Qin, P.; Wang, H.; Yang, X.; He, L.; Müller, K.; Shaheen, S.M.; Xu, S.; Rinklebe, J.; Tsang, D.C.; Ok, Y.S. Bamboo-and pig-derived biochars reduce leaching losses of dibutyl phthalate, cadmium, and lead from co-contaminated soils. Chemosphere 2018, 198, 450–459. [Google Scholar] [CrossRef]
  52. Steiner, C.; Das, K.; Melear, N.; Lakly, D. Reducing nitrogen loss during poultry litter composting using biochar. J. Environ. Qual. 2010, 39, 1236–1242. [Google Scholar] [CrossRef] [Green Version]
  53. Li, Z.; Delvaux, B.; Yans, J.; Dufour, N.; Houben, D.; Cornelis, J.T. Phytolith-rich biochar increases cotton biomass and silicon-mineralomass in a highly weathered soil. J. Plant Nutr. Soil Sci. 2018, 181, 537–546. [Google Scholar] [CrossRef]
  54. Duan, R.; Hu, H.; Fu, Q.; Kou, C. Remediation of Cd/Ni contaminated soil by biochar and oxalic acid activated phosphate rock. Huan Jing Ke Xue Huanjing Kexue 2017, 38, 4836–4843. [Google Scholar] [PubMed]
  55. Rees, F.; Simonnot, M.-O.; Morel, J.-L. Short-term effects of biochar on soil heavy metal mobility are controlled by intra-particle diffusion and soil pH increase. Eur. J. Soil Sci. 2014, 65, 149–161. [Google Scholar] [CrossRef]
  56. Dong, X.; Wang, C.; Li, H.; Wu, M.; Liao, S.; Zhang, D.; Pan, B. The sorption of heavy metals on thermally treated sediments with high organic matter content. Bioresour. Technol. 2014, 160, 123–128. [Google Scholar] [CrossRef]
  57. Tang, J.; Zhu, W.; Kookana, R.; Katayama, A. Characteristics of biochar and its application in remediation of contaminated soil. J. Biosci. Bioeng. 2013, 116, 653–659. [Google Scholar] [CrossRef]
  58. Sui, F.; Zuo, J.; Chen, D.; Li, L.; Pan, G.; Crowley, D.E. Biochar effects on uptake of cadmium and lead by wheat in relation to annual precipitation: A 3-year field study. Environ. Sci. Pollut. Res. 2018, 25, 3368–3377. [Google Scholar] [CrossRef]
  59. Pfister, M.; Saha, S. Effects of biochar and fertilizer management on sunflower (Helianthus annuus L.) feedstock and soil properties. Arch. Agron. Soil Sci. 2017, 63, 651–662. [Google Scholar] [CrossRef]
  60. Steiner, C.; Glaser, B.; Geraldes Teixeira, W.; Lehmann, J.; Blum, W.E.; Zech, W. Nitrogen retention and plant uptake on a highly weathered central Amazonian Ferralsol amended with compost and charcoal. J. Plant Nutr. Soil Sci. 2008, 171, 893–899. [Google Scholar] [CrossRef]
  61. Githinji, L. Effect of biochar application rate on soil physical and hydraulic properties of a sandy loam. Arch. Agron. Soil Sci. 2014, 60, 457–470. [Google Scholar] [CrossRef]
  62. Qayyum, M.F.; ur Rehman, M.Z.; Ali, S.; Rizwan, M.; Naeem, A.; Maqsood, M.A.; Khalid, H.; Rinklebe, J.; Ok, Y.S. Residual effects of monoammonium phosphate, gypsum and elemental sulfur on cadmium phytoavailability and translocation from soil to wheat in an effluent irrigated field. Chemosphere 2017, 174, 515–523. [Google Scholar] [CrossRef]
  63. Huang, G.; Ding, C.; Zhou, Z.; Zhang, T.; Wang, X. A tillering application of zinc fertilizer based on basal stabilization reduces Cd accumulation in rice (Oryza sativa L.). Ecotoxicol. Environ. Saf. 2019, 167, 338–344. [Google Scholar] [CrossRef]
  64. Liu, T.; Liu, Z.; Zheng, Q.; Lang, Q.; Xia, Y.; Peng, N.; Gai, C. Effect of hydrothermal carbonization on migration and environmental risk of heavy metals in sewage sludge during pyrolysis. Bioresour. Technol. 2018, 247, 282–290. [Google Scholar] [CrossRef] [PubMed]
  65. Saletnik, B.; Zaguła, G.; Bajcar, M.; Tarapatskyy, M.; Bobula, G.; Puchalski, C. Biochar as a multifunctional component of the environment—a review. Appl. Sci. 2019, 9, 1139. [Google Scholar] [CrossRef] [Green Version]
  66. Eslami, M.; Deghanzadeh, H.; Najafi, F. The effect of drought stress on oil percent and yield and the type of sunflower (Helianthus annuus L.) fatty acids. Agric. Sci. Dev. 2015, 4, 1–3. [Google Scholar]
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Figure 1. Effect of zinc nanoparticles and biochar of rice-straw and cow-manure on soil pH, EC, organic matter (A), and available heavy metals (B) after harvesting sunflowers grown in soil irrigated with wastewater for long-term (Data are the combined statistical analysis over the two seasons). Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, DM = dry matter, Error bars = Standard error of means (SEM). Means with different superscripts a−e for the same color of columns are significantly different at probability (p) ≤ 0.05.
Figure 1. Effect of zinc nanoparticles and biochar of rice-straw and cow-manure on soil pH, EC, organic matter (A), and available heavy metals (B) after harvesting sunflowers grown in soil irrigated with wastewater for long-term (Data are the combined statistical analysis over the two seasons). Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, DM = dry matter, Error bars = Standard error of means (SEM). Means with different superscripts a−e for the same color of columns are significantly different at probability (p) ≤ 0.05.
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Figure 2. Effect of zinc nanoparticles and biochar of rice-straw and cow-manure on heavy metals accumulation in biomass of sunflowers grown in soil irrigated with wastewater over a long-term period (Data are the combined statistical analysis over the two seasons). Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, DM = dry matter, Error bars = Standard error of means (SEM). Means with different superscripts a–e for the same color of columns are significantly different at probability (p) ≤ 0.05.
Figure 2. Effect of zinc nanoparticles and biochar of rice-straw and cow-manure on heavy metals accumulation in biomass of sunflowers grown in soil irrigated with wastewater over a long-term period (Data are the combined statistical analysis over the two seasons). Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, DM = dry matter, Error bars = Standard error of means (SEM). Means with different superscripts a–e for the same color of columns are significantly different at probability (p) ≤ 0.05.
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Figure 3. Effect of zinc nanoparticles, and biochar of rice-straw and cow-manure on total chlorophyll content (SPAD) of sunflowers grown in soil irrigated with wastewater for long-term (Data are the combined statistical analysis over the two seasons). Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, Bars = Standard error of means (SEM), DAS = Days after sowing.
Figure 3. Effect of zinc nanoparticles, and biochar of rice-straw and cow-manure on total chlorophyll content (SPAD) of sunflowers grown in soil irrigated with wastewater for long-term (Data are the combined statistical analysis over the two seasons). Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, Bars = Standard error of means (SEM), DAS = Days after sowing.
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Agronomy 10 00790 g004 550
Figure 4. Effect of zinc nanoparticles, and biochar of rice-straw and cow-manure on proline content (A) and total leaf area (B) of sunflowers grown in soil irrigated with wastewater for long-term. Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, FW = fresh weight. SEM = Standard error of means, Means with different superscripts a–e are significantly different at p ≤ 0.05. Tukey’s test was applied to compare means.
Figure 4. Effect of zinc nanoparticles, and biochar of rice-straw and cow-manure on proline content (A) and total leaf area (B) of sunflowers grown in soil irrigated with wastewater for long-term. Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, FW = fresh weight. SEM = Standard error of means, Means with different superscripts a–e are significantly different at p ≤ 0.05. Tukey’s test was applied to compare means.
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Table
Table 1. Physicochemical characteristics of experimental soil and biochar.
Table 1. Physicochemical characteristics of experimental soil and biochar.
Soil
(Season 1)		Soil
(Season 2)		Rice Straw BiocharCow Manure Biochar
pH7.167.228.318.95
EC (dS m−1)1.001.040.152.92
Total N (g kg−1)0.2010.2039.8114.32
Total P (g kg−1)--2.0511.42
Total K (g kg−1)--20.2618.34
Total carbon (g kg−1)--465.97409.32
Total magnesium (g kg−1)--3.75-
Total Si (g kg−1)--6.341-
Total Fe (g kg−1)0.0710.077--
Available N (mg kg−1)26.4426.54122.09242.94
Available P (mg kg−1)6.806.97--
Available K (mg kg−1)45.1645.19--
Organic matter (%)2.292.3725.9729.78
Specific surface area m2 g−1--24.14 30.11
Water holding capacity (%)--35.0142.29
Trace elements (mg kg−1)
As0.040.04ndnd
Pb14.3014.38nd0.09
Cd3.013.09nd0.01
Cr39.4639.440.020.08
Ni40.9040.920.020.04
Cu43.7043.9211.7826.43
Zn54.0754.6939.8653.29
Table
Table 2. Effects of zinc nano-particles, plant-, and animal-biochars on growth, and yield and its components of sunflower grown in soil irrigated with wastewater over the long-term.
Table 2. Effects of zinc nano-particles, plant-, and animal-biochars on growth, and yield and its components of sunflower grown in soil irrigated with wastewater over the long-term.
TraitsStem Diameter (cm)Plant Height (cm)Head Diameter (cm)Number of Seeds Per Head100-Seed Weight (g)Seed Yield (kg ha −1)
Treatment
Season 2017
Control2.09 d180.1 e17.7 c953.3 e5.07 c2075.7 e
Zn NPs2.17 d193.2 d18.5 c1040.3 d5.40 c2481.4 d
RSB2.36 c216.9 c22.3 b1213.9 c6.39 b2531.0 c
CMB2.45 b220.5 b23.1 b1336.1 b7.15 a2652.8 b
Combination2.70 a241.9 a28.0 a1441.0 a7.44 a2953.0 a
LSD0.050.082.20.935.20.3439.8
Significant***********
Season 2018
Control2.13 d182.5 e17.3 c958.3 e5.09 c2093.3 e
Zn NPs2.19 d198.2 d18.5 c1046.3 d5.44 c2506.6 d
RSB2.34 c214.5 c22.1 b1205.7 c6.37 b2545.0 c
CMB2.43 b224.5 b23.5 b1340.5 b7.21 a2664.4 b
Combination2.80 a239.7 a28.4 a1435.0 a7.50 a2991.2 a
LSD0.050.072.71.539.40.3632.5
Significant***********
Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, LSD0.05 = least significant differences at 5% level. Means with different superscripts a–e within each column are significantly different at probability (p) ≥ 0.05 (not significant), p ≤ 0.05 (*), p ≤ 0.01 (**), Tukey’s test was applied to compare means.
Table
Table 3. Effect of zinc nano-particles, plant-biochars, and animal-biochars on oil percentage and its quality of sunflowers grown in soil irrigated with wastewater for the long-term.
Table 3. Effect of zinc nano-particles, plant-biochars, and animal-biochars on oil percentage and its quality of sunflowers grown in soil irrigated with wastewater for the long-term.
Traits
Treatments		Oil
(%)		Oil
(kg ha−1)		Oleic Acid (%)Linoleic Acid (%)Oleic/Linoleic Ratio
Season 2017
Control32.81 d681.0 d81.15 c8.61 a9.43 d
Zn NPs35.56 c882.4 c82.37 c7.94 a10.37 c
RSB35.42 c896.5 c86.18 b4.43 b19.45 b
CMB37.18 b986.3 b86.09 b4.32 b19.93 b
Combination41.10 a1213.7 a91.20 a2.40 c38.00 a
LSD0.050.9245.31.320.930.72
Significant**********
Season 2018
Control32.91 d688.9 d81.23 c8.59 a9.46 d
Zn NPs35.54 c890.8 c82.41 c7.86 a10.48 c
RSB35.38 c900.4 c86.20 b4.49 b19.20 b
CMB37.26 b992.8 b86.05 b4.30 b20.01 b
Combination41.12 a1230.0 a91.28 a2.48 c36.81 a
LSD0.050.8938.21.340.900.83
Significant**********
Zn NPs = Zinc nano-particles, RSB = Rice straw biochar, CMB = Cow manure biochar, LSD0.05 = least significant differences at 5% level. Means with different superscripts a-d within each column are significantly different at probability (p) ≥ 0.05 (not significant), p ≤ 0.01 (**), Tukey’s test was applied to compare means.
Table
Table 4. Simple correlation coefficient (r) between available heavy metals in soil at harvest, heavy metals accumulation in sunflower, seed yield, growth, and quality traits (overall treatments) as an average of the two seasons.
Table 4. Simple correlation coefficient (r) between available heavy metals in soil at harvest, heavy metals accumulation in sunflower, seed yield, growth, and quality traits (overall treatments) as an average of the two seasons.
Available Heavy Metals in Soil Post-HarvestHeavy Metals Accumulation in SunflowerProline (9)Leaf Area (10)Seed Yield ha−1 (11)Oil % (12)Oleic Acid (13)Linoleic Acid (14)
Zn (1)Cu (2)Cr (3)Cd (4)Zn (5)Cu (6)Cr (7)Cd (8)
1 −0.964 **−0.980 **−0.985 **0.843−0.897 *-0.936 *−0.883 *0.950 *0.950 *0.890 *0.915 *0.965 **−0.963 **
2 0.984 **0.991 **−0.7600.8600.889 *0.880 *−0.883 *−0.907 *−0.881 *−0.857−0.975 **0.998 **
3 0.992 **−0.8640.936 *0.933 *0.913 *−0.939 *−0.968 **−0.929 *−0.932 *−0.997 **0.981 **
4 −0.8180.894 *0.939 *0.919 *−0.936 *−0.939 *−0.919 *−0.906 *−0.979 **0.993 **
5 −0.979 **−0.909 *−0.8690.939 *0.960 **0.920 *0.982 **0.874−0.759
6 0.922 *0.898 *−0.944 *−0.990 **−0.947 *−0.986 **−0.949 *0.855
7 0.980 **−0.993 **−0.944 *−0.977 **−0.968 **−0.915 *0.904 *
8 −0.954 *−0.907 *−0.991 **−0.939 *−0.898 *0.900 *
9 0.967 **0.964 **0.983 **0.925 *−0.893 *
10 0.945 *0.985 **0.973 **−0.903 *
11 0.970 **0.924 *−0.894 *
12 0.933 *−0.861
13 −0.968 **
14
*, ** Significant and highly significant at 5%, respectively.

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MDPI and ACS Style

Seleiman, M.F.; Alotaibi, M.A.; Alhammad, B.A.; Alharbi, B.M.; Refay, Y.; Badawy, S.A. Effects of ZnO Nanoparticles and Biochar of Rice Straw and Cow Manure on Characteristics of Contaminated Soil and Sunflower Productivity, Oil Quality, and Heavy Metals Uptake. Agronomy 2020, 10, 790. https://doi.org/10.3390/agronomy10060790

AMA Style

Seleiman MF, Alotaibi MA, Alhammad BA, Alharbi BM, Refay Y, Badawy SA. Effects of ZnO Nanoparticles and Biochar of Rice Straw and Cow Manure on Characteristics of Contaminated Soil and Sunflower Productivity, Oil Quality, and Heavy Metals Uptake. Agronomy. 2020; 10(6):790. https://doi.org/10.3390/agronomy10060790

Chicago/Turabian Style

Seleiman, Mahmoud F., Majed A. Alotaibi, Bushra Ahmed Alhammad, Basmah M. Alharbi, Yahya Refay, and Shimaa A. Badawy. 2020. "Effects of ZnO Nanoparticles and Biochar of Rice Straw and Cow Manure on Characteristics of Contaminated Soil and Sunflower Productivity, Oil Quality, and Heavy Metals Uptake" Agronomy 10, no. 6: 790. https://doi.org/10.3390/agronomy10060790

APA Style

Seleiman, M. F., Alotaibi, M. A., Alhammad, B. A., Alharbi, B. M., Refay, Y., & Badawy, S. A. (2020). Effects of ZnO Nanoparticles and Biochar of Rice Straw and Cow Manure on Characteristics of Contaminated Soil and Sunflower Productivity, Oil Quality, and Heavy Metals Uptake. Agronomy, 10(6), 790. https://doi.org/10.3390/agronomy10060790

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