The soil sample for this study was randomly collected from an abandoned lead smelting slag contaminated site in Ibadan, Nigeria. The site lies between longitude 7˚24'N and latitude 4˚00'E at an elevation of 174 m above sea level. The large expanse of agricultural land in this area has been made unproductive due to the impact of the LSS illegally dumped on the land several years ago. Soils were sampled at different points at 15 cm depth and mixed to form composite sample which was transported to the laboratory.

The biochars were produced from rice husk and cashew nut shell. These agricultural residues were chosen due to their abundance in Nigeria and in other places in the world. Their use as biochar sources will minimise the problem of managing their waste. Compost was prepared from wild sunflower (Tithoniadiversifolia) and poultry liter in ratio 3:1 of sunflower to poultry manure for 12 weeks [9] . The different agricultural residues (rice husk and cashew nut shell) collected were pyrolysed locally in the presence of low oxygen using a simple, low cost two barrel charcoal retort method [16] at approximate pyrolysis temperature between 450˚C and 500˚C). The produced chars were ground to fine powder and sieved through a 2 mm sieve.

The soil samples were air-dried at room temperature for two weeks, mechanically ground and sieved to <2 mm. The <2 mm fraction soil samples were analysed for physicochemical parameters. Organic carbon was determined using potassium dichromate method [17] . pH was measured in water at soil: water ratio of 1:1 using pH meter. Particle size analysis was determined by hydrometer method. To determine the total environmentally available Pbconcentrations in the soil and amendments, one gramme of soil was acid digested with 10 mL 2 M HNO₃ for 2 hours at 90˚C - 100˚C [5] . In order to solubilise the minerals in the biochars and compost, there is need to destroy the organic matter contents. To achieve this, one gramme each of biochars and compost was ashed in a muffle furnace for 6 hours at a temperature between 450˚C - 500˚C. The ash was dissolved in 10 mL of 2 M HNO₃, filtered with Whatman filter paper No. 2 (8 µm) and made up to mark in 25 mL volumetric flask [18] . The total environmentally available Pb concentration in soil and amendments digests was determined by atomic absorption spectrophotometer (Buck scientific model 210A) with air-acetylene flame. Exchangeable cations (Ca, Mg, Na, K) were extracted using 0.2 M Silver thiourea solution [19] . Potassium and Na were determined with a flame photometer (Jenway, PFP7) while Ca and Mg were measured using atomic absorption spectrophotometer. The cation exchange capacity was determined by the sum of the exchangeable bases including Ca, Mg, K and Na [20] . Kjedahl’s method was used to determine nitrogen content [21] . Phosphorus was determined by Mehlich III method [22] . Two grammes (2.0 g) of air-dried soil sieved to pass through ˂2 mm were extracted with 20 mL of Mehlich-3 extracting solution [0.2 M Glacial acetic acid (CH₃COOH), 0.25 M Ammonium nitrate (NH₄NO₃), 0.015 M Ammonium fluoride (NH₄F), 0.013 M Nitric acid (HNO₃), 0.001 M ethylene diamine tetraacetic acid (EDTA) at pH = 2.5 ± 0.05] on a mechanical shaker at 120 rpm for 5 minutes. The suspension was filtered using Whatman filter paper No. 2. The phosphorus content was determined colorimetrically by molybdenum blue ascorbic acid method. The results of physicochemical properties of the soil, biochars and compost are reported in Table 1.

0.01 M CaCl₂ batch leaching experiment was conducted to optimize Pb stabilisation potentials of biochars,

-Not available, TOC―Total organic carbon content, CEC―Cation exchange capacity.

compost and compost-modified biochars in terms of the amount added to the contaminated soil. 0.0 g (contaminated soil without amendment), 0.05 g, 0.1 g, 0.2 g, 0.4 g of each biochar and compost was added singly and in combination with compost to 1.00 g of contaminated soil in 50 mL polycarbonate centrifuge tube. 5 mL of 0.01 M CaCl₂ solution was added and the solution was shaken for 2 hrs at 160 rpm using an orbital shaker, after which the solution was filtered using Whatman filter paper No. 2. The filtrates were analysed for Pb concentration using atomic absorption spectrophotometer (Buck scientific model 210A). The percent stabilisation efficiencies of the amendments were calculated.

Pot experiment was set up in a greenhouse to study the effect of biochars and compost both singly and in combination (equal proportion by weight using the minimum dose) on soil Pb stabilisation, maize plant growth and Pb accumulation. For comparison, the most effective dose (0.4 g) and the minimum dose (0.05 g) of the amendments from the batch leaching test were selected for the pot experiment. The amount of biochars and compost required were calculated with regards to the amount of soil used for planting (500 g) based on the results of the optimisation. This was equivalent to 25 g (50 g for combination) and 200 g of amendment per 500 g of soil to represent 0.05 and 0.4 g amendment/g soil rates respectively. Altogether there were 9 treatments and each treatment was performed in duplicate, giving a total of 18 bags. No extra macronutrient treatment from external source was applied to the soils.

The amendments were thoroughly mixed with the soils and transferred into 30 cm diameter polyethylene bags. Each bag was placed in a plastic bowl to prevent loss of leachate from the system and water was applied to each bag until soil reached 70% water holding capacity after which they were allowed to equilibrate for one week. During the period of one week the bags were watered every two days (approximately 100 - 200 mL). After one week, the soil was sown with two maize seeds but the survival of the seedlings to the end of the experiments was dependent on the type and rates of the amendments. Watering of the plants was done at two days intervals. The leachate collected in each saucer was also returned to the experimental soil when necessary to prevent loss of the metal. At six weeks of planting, agronomical parameters such as plant height, number of leaves and leaf area were taken. After 6 weeks, plants were harvested. The roots of the maize plants were washed with distilled water to remove soil, the plant were separated into shoot and root and oven-dried for 3 days at 80˚C. The dry biomass was determined. After biomass determination, the oven-dried plant parts were ground. Depending on the root dry weight of the plant ≤ 1.00 g of each was ashed in a muffle furnace for 6 hours at a temperature between 450˚C - 500˚C for Pb determination [18] . The experimental soils were also analysed for the total environmentally available Pb [5] . Data were analysed using descriptive statistics.

The physico-chemical properties of the soil, biochars and compost are Table 1 presents. The pH of unamended soil was 5.7 which showed that the soil was acidic.

The pH of CNSB is slightly acidic (6.30) compared to the pH of rice RHB and compost which are alkaline. The acidic pH of CNSB can be attributed to its anacardic acids content [23] . The organic carbon of the soil was as low as 1.80%, which could be attributed to the high content of the slag which prevented vegetation of the soil. The concentration of Pb in the untreated soil was 18,300 mg/kg. Compost, RHB and CNSB have low Pb contents of 1.50, 0.90 and 1.2 mg/kg respectively, suggesting that there is no considerable contribution of Pb level when these materials are applied to the soil. The biochars and compost have high levels of Ca, Mg, N, P, K and CEC which was expected to improve the soil condition and enhance plant growth on application. The physico- chemical parameters present the proposed amendments as non-hazardous, as potential soil nutrients sources and as heavy metal stabilisers.

The control and the amended soils at the different doses were subjected to 0.01 M CaCl₂ solution extraction to determine extractable Pb. The extractable Pb was highly dependent on the dose and the amendment type. The results are summarized in Figure 1.

As can be observed, increase in amendments doses from 0.05 to 0.4 g/g soil decreased the extractable Pb concentrations from 60 mg/kg in the control soil to non-detectable levels in the Compost, CNSB, Compost- modified biochars and to 0.55 mg/kg in the RHB treated soils.

To evaluate the efficiency of the treatments on the stabilisation of Pb in the soil and bioavailability in plant, maize plants were grown for six weeks on the untreated and treated soils. It must be noted that although maize plant would not generally be considered as appropriate plant to evaluate treatment efficiency, it was used because it is a known lead accumulator [24] . This implies that if reduction in bioavailable Pb levels could be achieved with an accumulator through the application of the amendments on the contaminated soil, then it will possibly be better with other plants and the remediation plan will be judged successful. The growth parameter, that is, plant height, number of leaves and leaf area for the plants grown on the control and amended soils were measured and the results are presented in Figure 2.

Maize growth was enhanced by the amendments except with higher rate of CNSB. There are variations in the mean plant height, number of leaves and leaf area ranging from 40 ± 11 to 90 ± 1 cm, 2 ± 1 to 8 ± 1 and 70 ± 8 to 280 ± 11 cm² respectively among the plants grown on the soils. From the results, evidence of stunted growth perhaps due to Pb toxicity and the acidic nature of the soil were observed with plants grown on the control soil and the soil treated with higher rates of CNSB.

Plants grown on the soil that was amended with higher rate of CNSB showed mean height of 40 cm compare with 50 cm in the control, 2 leaves compared with 3 leaves in the control and an area of 70 cm² compared with 86 cm² in the control. The condition did not improve with addition of compost at this rate.CNS biocharis acidic as shown in Table 1. This likely had negative effect on the growth of the plant. On the other hand, compost, RHB and compost-modified RHB thrived with the three rates. The plants grown on them displayed healthy outlook and taller height with higher number of leaves and leaf areas. Plant parameters performed better with mixture of compost and the biochars at lower rates of 50 g/500g soil than when the two biochars were used singly at very high rates of 200 g/500g soil. The reason for this observation may be due to the combined effect of CEC and alkalinity impacted on the soil by the compost-modified RHB. As can be observed in Table 1, compost had the highest CEC followed by RHB and then CNSB. Cation exchange capacity of the amendments reflected their potential nutrient holding capacity. The combining effects of nutrient holding capacities of compost and RHB on making the contaminated soil fertile yielded healthier plants.

The response of maize plant in terms of root and shoot dry biomass is presented in Figure 3. In view of the

amendment type and rate, compost alone promoted the highest root and shoot biomass. For all other treatments, with the exception of CNSB at the rate of 200 g/500g the root and shoot biomass yields were higher than those of the control plant.

Cashew nut shell biochar at the highest rate (200 g/500g) produced the least root (0.1) and shoot (0.25) biomass values. However, addition of compost to the CNSB even at a lower rate (50 (1:1) g/500g) improved the performance of the biochar with 0.65 root and 1.45 shoot biomass values. The observed less performance of the CNSB may be associated with its acidic nature, the condition which is not favourable for plant growth. Unlike CNSB, the pH values of both compost (8.70) and RHB (7.40) are alkaline. The observed desirable performance of compost-modified CNSB may also be connected to this alkaline nature of compost which increased the pH of CNSB and therefore favours plant growth. This suggests that pH of the biochar is an important factor to consider when developing biochar remediation of heavy metals contaminated soils.

The concentrations of Pb measured in soil, maize plant root and shoot after harvesting are shown in Table 2.

CNSB = Cashew nut shell biochar; RH B = Rice husk biochar; C = Compost.

Total soil Pb content was reduced from 15,340 mg/kg in the control soil after harvesting to concentrations which ranged from 8250 (C2) to 12,750 mg/kg (CNSB1) in the treated soils.

Similarly, total root Pb content was reduced from 2260 mg/kg to concentrations which ranged from 200 (RHB1/C1) to 950 mg/kg (C1). Furthermore, total shoot Pb content was reduced from 530 mg/kg to concentrations which ranged from 74 (RHB1/C1) to 390 mg/kg (C1). The results demonstrate that compost performed best in terms of stabilisation of Pb in soil while the compost-modified biochars particularly mixture of rice husk biochar and compost at lower rate performed better at reducing Pb available in maize plant. This was followed by the two biochars when used singly. The soil Pb levels in soil amended with higher rates (200 g/500g) of compost and amendments were the least. This perhaps was due to dilution effect which high rate of amendment could produce on the contaminant in soil [25] . However, this high application rate may not be applicable in real field conditions. Overall, application of compost-modified RHB performed best in terms of both stabilisation of Pb in soil and reduction in plant available Pb.

The observed decrease in the concentration of Pb in the soil, plant root and shoot may be associated with some inherent factors of the different amendments which changed the chemistry of the soil. The factors among others include the pH, organic matter and the chemical components of the amendments.

Sabilisation of Pb in soil can be achieved through adsorption, complexation and precipitation which are influenced by the pH, dissolved organic carbon (humic substances) and mineral components of the amendments and soil respectively. At lower pH of the soil, there is an increase in the H⁺ ion concentrations and it is expected that H⁺ ion will compete with adsorption of Pb on the surface of the amended soil, thus decreasing stabilisation of Pb in the soil. At high pH, OH^-ion increases which favours soil stabilisation of Pb. The acidic to near neutral pH (6.30) of CNSB coupled with acidity (pH = 5.70) of the soil implies competition of H⁺ with Pb on the surface of the CNSB amended soil, hence less Pb stabilisation. On the other hand, addition of compost and RHB to the soil was expected to increase the pH of the soil due to their alkaline pH, implying an increase in the negative sites of the soil which favoured Pb stabilisation.

Compost and biochars contain dissolved organic matter (humic and fulvic acids) which also possibly enhanced stabilisation of Pb in soil. High ability of Pb to form more stable coordination complexes with humicacids has been documented [26] . Previously reported Fourier Transform Infrared(FTIR) studies on the organic constituents of compost and rice husk derived residues show that they contain organic functional groups such as alcohols, phenols, carboxylic acids and esters [27] - [29] . These functional groups would have become ionised at high pH and formed negatively charged ions which stabilized Pb. The degree of stabilisation depends on the availability of the organic compounds in soil. Organic matter in biochars breaks down slowly to form dissolved organic matter (humic substances). This may explain the lower stabilisation of Pb in biochar amended soil when compared with compost amended soils. The release of dissolved organic matter in compost is faster due to the action of microorganisms, which implies higher concentrations in soil with more binding rates with soil Pb. This probably accounts for enhanced Pb stabilsation in compost amended soil (Table 2).

Inorganic chemical composition of the amendments perhaps also played a important role in the stabilisation of Pb in the soil and uptake by plant. As presented in Table 1, compost had a high phosphorus content. Phosphorus reacts with Pb in soil to form pyromorphite [Pb₅(PO₄)₃OH], the most stable compound of Pb in the environment [30] . Xu et al. [28] identified peaks that were associated with and in FTIR spectra of Rice husk- derived biochar. This suggests that stabilisation of Pb through precipitation of lead as carbonate and phosphate is a possibility. Typical XRF chemical characterisation of RH ash revealed that it contains up to 92% SiO₂ [31] . The result of this study also showed that RHB contained a high amount (9780 mg/kg) of Ca (Table 1). In a study by Wu et al. [27] , XRD pattern of rice husk-derived biochar also indicates the presence of inorganic components such as CaCO₃, KCl and SiO₂. Following these obtained and documented results, Pb stablisation in the RHB amended soils may also be attributed to encapsulation of Pb in the calcium silicate hydrate (C-S-H) gel formed from the pozzolanic reaction of Ca with the silica content of RHB in an alkaline environment of the soil [32] . Thus, this prevented Pb from becoming available in compost-RHB amended soil. Nevertheless, further investigations are required to justify or reject these assumptions.

The results of uptake of Pb in maize plant grown both on the control and amended soils are shown in Table 2. The root and shoot Pb concentrations in the untreated soil were substantially higher than those in the treated soils. In the plants that were grown on the control soil, Pb concentrations of 2260 and 530 mg/kg were observed in the root and shoot respectively. All the amendments reduced maize plant Pb uptake, although to different extents. The least Pb uptake by maize was observed in the soil treated with compost-modified RHB followed by compost-modified CNSB, RH-biochar, CNS-biochar and then compost. Compost-modified RH-Biochar at the rates of 50 g/500g soil lowered the root concentrations by 91%. Similarly, it reduced the shoot Pb from 530 mg/kg to 74 (86.0%). The results suggest that compost-modified biochars performed better than the amendments being used singly. It is interesting to note that stabilisation of Pb in soil amended with compost is better than stabilisation of Pb in biochar amended soils. However, uptake by plant is higher in compost treated soils. This may be attributed to higher humic substances (humic and fulvic acids) contained in the compost. Fulvic acids (FAs) are smaller than humic acids (HAs) and are more chemically reactive than HAs. Due to their smaller size, they can enter plant roots and shoots readily thereby carrying along heavy metals. As cited by Boruvka and Drabek [26] , heavy metals bound on insoluble humic substances are relatively immobile. On the other hand, binding on smaller organic molecules may increase metal mobility and bioavailability. Considering the results of this pot experiments, it can be deduced that remediation of Pb contaminated soil with compost-modified biochar has great potential to reduce bioavailable Pb.