ARTICLE INFORMATION	ABSTRACT
Article history:  Received: 01.08.2021 Accepted: 13.09.2021 Published: 31.10.2021  *Corresponding author:  E-mail:   ngadiruffin@gmail.com Phone:   +243 816915111  Keywords:	The study aims to evaluate the level of vegetable crop contamination located along high-frequency motorized roadways.  The useful area for a secure culture will be determined according to the threshold of toxic metal traces. The findings show that: the level of vegetable crop contamination varies according to the distance separating the roadways from the cultivated plants; the lead rate is inversely proportional to the distance which separates the vegetable crops from Kasavubu and Saio roadways. In the soil,  lead concentrations are higher than in vegetables and irrigation water. The non-soil renewal after the harvest period could justify the accumulation of lead in the soil. Cadmium is only detected in soil samples taken less than 3 m away from the road. Tire wear could be the real cause, the kinetic Cadmium differential, and  Arsenic is zero, while an inverse correlation was observed between the physicochemical parameters (pH, OM, and TOC) and the metals under study. The correlation between lead in soil and vegetables is justified by the same source of contamination. This is not the case for trace metals in irrigation water and vegetables. The useful area for safe cultivation is set at 50 m away from the frequent motorized road.

INTRODUCTION  

According to the estimates of Institut  National de Statistique (National Statics  Institute of Statistics) in the DRC, the city of  Kinshasa had 6,062,000 inhabitants in 2000.  Referring to the the1973 statistics which report the figure of 1,198,720 inhabitants,  the demography recorded an exponential growth (Flouriot, 1975; Lelo, 2008;  Wagemakers et al., 2010). Currently, the population is estimated at over 10 million  (Musibono et al., 2011). 

Due to the increase sharp of the world population in general, and urban in particular, food for cities has become a basic problem (Bricas and Seck, 2004; Mougeot,  2005). This urban population growth concerns both capitals and secondary cities  (Aubry et al., 2010). 

The population of the City of Kinshasa consumes around 155,500 tons of vegetables a year, with an increase of 3 to 5% per year.  In order to meet this need, the population resorts to urban agriculture. This activity is a  response to poverty and food insecurity  (FAO, 2007). Ignored for a long time, urban agriculture is increasingly seen by urban planners as one of the means to tackle food inequality. It provides income to urban populations  (Dubbeling, 2009, Musibono et al., 2011). 

Growing cities, edible plants involve exposure to constraints such as optimizing the available space and controlling the exposure of populations to pollutants often observed in different environments (soil, water, air). As cities are densely populated,  the likelihood of human exposure to the present pollutants is relatively high.  Scenarios of human exposure to pollutants commonly observed in urban areas are particularly the ingestion of water from polluted wells the consumption of vegetable plants grown on polluted soils  (Shahid et al., 2016), or having intercepted enriched atmospheric particles in metals  (Schreck et al., 2014; Xiong et al., 2016). 

Environmental pollution is still widely observed in urban areas following historical pollution of lead, Cadmium, or very persistent mercury in soils (Leveque et al., 2015, Dumat et al., 2016) or atmospheric deposition of particulate pollutants. Over long distances (Schreck et al., 2013). Many chemicals can circulate or accumulate in  garden soils (Schwartz, 2013), and finally,  vegetables (Uzu et al., 2014; Clinard et al., 2015; Xiong et al., 2016). 

Air pollution by heavy metals is riffed in urban areas, not only because of industry concentration and domestic households but also because of the density of motor vehicle traffic (Hanane et al., 2015). The main metallic pollutants emitted in the road environment come from fuels, tires, linings, and brakes (Pagotto, 1999; Deletraz, 2002).  The use of lead in gasoline, however, is still common in developing countries (Menkes and Fawcett, 1997). The entry of lead into the manufacture of batteries and fuels led to an increase in its atmospheric concentration  (Rhue et al., 1992).

Pollutants from automobile traffic or district heating can be deposited on plants or soil or even absorbed by plant roots (Wieczorek et al., 2005; Kalavrouziotis et al., 2007). On the one hand, trace metallic elements (Pb,  As, Hg, Cd, Zn, Cu, Ni, and Cr) accumulate as circulation increases. On the other hand,  hydrocarbons, oils, and rubbers constitute polycyclic aromatic hydrocarbons (PAHs)  (Barriusto et al., 1996, Barbaste et al., 2004).

Regardless of road traffic, contaminants from fertilizers, pesticides, and nature are absorbed by vegetation and then end up in the trophic chain (Atidegla et al., 2011). An assessment of the air pollution of crops and the use of untreated urban solid waste,  fertilizers, and pesticides is needed to improve the quality of vegetables grown in market gardening sites in Kinshasa. 

The curves obtained for the trace metals will  make it possible to distinguish two zones: 

∙ Red zone characterized by a high rate  of contamination compared to  standards; 

∙ Useful area where contaminants in crop plants are at the minimum acceptable trace level. 

If the circumcised area is red, the municipal or urban authority will have to draw up legislation on urban agriculture. The study aims to evaluate the quality of vegetables grown near Kasavubu and Saïo roadways and consumed in Kinshasa. 

Site 

Located on the crossroads of KASAVUBU and  SAIO avenues in KASAVUBU municipality, this site is frequently used by motorized vehicles.  It is also used as a house for street children who discharge excrement and urine there. 

Figure 1. Cultivation site 

Market gardeners cultivate amaranth  (Amaranthus hybridus), spinach (Basella alba), sweet potato (Ipomoea batatas), and sorrel (Hibiscus acetocella). Market gardeners use well water for watering.  Regarding fertilization, they use litter,  poultry droppings, or other chemical fertilizers (NPK, urea, etc.) and untreated household waste to optimize yield. The choice of Amaranthus hybridus cultivation is justified by the fact that it represents 90% of market gardening activities in Kinshasa  (Wekole, 2018). 

MATERIALS

 Soil and plant samples were retrieved according to the distance separating them from the road (between 3m and 100m). After the removal of plant debris and roots, soil samples collected from organo-mineral horizons (0-10cm) of the soil were dried at room temperature, then crushed and sieved through the 2mm mesh. The vegetable samples were dried out of direct sunlight and then crushed.

The sauce was used for the analysis of the cooked vegetables. The water sample was taken from the wells selected on the basis of their position relative to the road. During the rainy season, the sampling took place between April 10 and 15, 2019, i.e. 25  days later. The second phase took place during the dry season (July 2019). 

METHODS  

The physicochemical parameters: total organic carbon and Organic matter of the soil were deduced using the weight difference method before and after kiln incineration  (Abderrazzak (2012). The physicochemical parameters of the well water were determined in situ using the HACH HQ 40d  brand multi-parameter probe. The soil pH was determined using a pH meter with  “combined pH electrodes”. The pH (H2O) is measured in a soil-water suspension while the pH-KCl is determined in a 1N soil-KCl suspension using the ST 10 0HAUS brand pH meter.

The analyzes of the trace metals (Pb, Cd, and  As) were carried out by molecular absorption spectroscopy using the DR 2000  spectrophotometer with digital reading applying the Beer-Lambert law, the detection limit of which is 0.02 mg/L. The heavy metals transfer to plants was  evaluated using the transfer factor according  to Tangou (2016): 

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To evaluate the relationship that exists between different analyzed parameters, a  statistical correlation study by PEARSON was used to find out if these parameters have the same origin or if the observed difference is due to chance. The ORIGIN 8 software was used for this assessment. 

The Student’s Test was applied to assess the variability of the parameters (distance between the red zone and useful zone) during the two seasons. It was calculated on the basis of a Microsoft Excel program (Ancelle,  2008). 

RESULTS

Physicochemical parameters for well water a. pH

Figure 2. pH of well water 

This figure shows the pH of the different wells used for watering the vegetables for both seasons. Well P3, has a high pH (6.74) and well P5 a low pH compared to the other wells. both seasons. In well P3, the high pH (6.74) 

a. Dissolved oxygen 

Figure 3. Evolution of dissolved oxygen in different water wells 

This Figure reveals that the dissolved oxygen values in the different wells used for watering the vegetables during the two seasons vary between 2.28 (P10) and 5.58  (P11). 

a. Conductivity 

Figure 4. Conductivity values in different water wells 

This Figure shows the different conductivity values in the wells used for watering vegetables. Thus, whatever the season, The P2 well has a high value (1164), and the P5  well has a lower value compared to the other wells.

a. Temperature 

Figure 5. Different temperature values in different water wells 

This figure shows different temperature values in water wells used for watering vegetables. Whatever the season, wells P1  and P9 have high-temperature values (31.5 ° C) while well P6 (28.9 ° C) has a low value compared to the other wells. 

a. Heavy metals in well water (Pb, Cd and As) 

Figure 6. Contaminant rates (Pb, Cd, and As) in different water wells 

– The results of this Figure indicate that: – The arsenic values are zero for wells  P4 to P8 and P10. But from P1 to P3,  P9 and P11 vary between 0.1 to 0.4  mg / L. 

– A high value of Cadmium in wells 6  (P6) and 12 (P12) and low in wells 3  (P3). It was found that in wells 9 (P9), the cadmium value is almost zero  compared to the analysis method  used; 

– Lead values are considerable in wells  P1 and P2 near the road compared to wells P3 to P11 which are further away from the road.

Soils 

a. Organic substances in the soil 

Figure 7. Evolution of organic substances in the soil regarding the distance function 

Figure 7 illustrates the evolution of organic substances in the soil as a function of distance. It reveals that from 30m, the standard error bar differs from the value recorded at 3m. The trend line is increasing. 

a. Total organic carbon in soil 

Figure 8. Evolution of total soil organic carbon in function to distance 

Figure 8 indicates the evolution of Total  Organic Carbon in the soil in the function of distance. It reveals that from 20m, the standard error bar differs from the value recorded at 3m. The trend line is increasing.

a. Soil pH (0-10cm) pH in the water-soil suspension 

Figure 9. Evolution of soil pH in the water-soil suspension 

Figure 9 shows the pH (H2O) values in the soil as a function of distance. It reveals that from 50m, the standard error bar differs from the value recorded at 3m. The trend line is increasing. 

pH in the water-KCl suspension 

Figure 10. Evolution of the pH in the water-KCl suspension 

Figure 10 shows the pH (KCl) values in the soil as a function of distance. It reveals that from 20m, the standard error bar differs from the value recorded at 3m. The trend line is increasing.

Lead in soil 

Figure 11. Evolution of lead into the soil in the function of distance 

Figure 11 shows the evolution of Pb into the soil in the function of distance. It reveals that from 20m, the standard error bar differs from the value recorded at 3m. The trend line is decreasing. 

Cadmium in soil 

Figure 12. Evolution of Cadmium in the soil 

Figure 12 shows the evolution of Cd into the soil in the function of distance. It reveals that from 5m, the standard error bar differs from the value recorded at 3m. The trend line is decreasing.

Arsenic in soil 

Need image

Figure 13. Evolution of Arsenic in the soil 

Figure 13 shows the evolution of Arsenic in the soil regarding the function of distance. It reveals that from 10m, the standard error bar differs from the value recorded at 3m. The trend line decreasing. 

Vegetable 

Average Pb, As, and Cd in Amaranthus hybridus 

Need Image

Figure 14. Evolution of ETM in Amaranth

Figure 14 shows the level of contaminating trace metals in Amaranth. It reveals that from 10m, the standard error bar differs from the value recorded at 3m. The trend line is decreasing. 

The absence of Cadmium and Arsenic levels 3m from the road is justified by the fact that the exhaust fumes only emit lead from the fuel. 

Table 1 below indicates that the lead transfer factor from soil to vegetables varies from 0.6  to 5.7 ranges from 3 to 50 m from the roadway. No transfer factors for Cadmium and Arsenic were observed. 

Table 1: Transfer factor (F) 

Distance (m)	Kasavubu and Saio Crossways
	Cd	As	Pb
3	n.d	n.d	0,6
5	n.d	n.d	0,7
10	!n.d	n.d	0,7
20	n.d	n.d	1,0
30	n.d	n.d	1,2
50	n.d	n.d	5,7
80	n.d	n.d	5,0
100			5,0

Disappearance of contaminants compared to distance 

need image

Figure 15. Disappearance rate of contaminants compared to the distance 

At a distance of 5m, the disappearance rate is respectively estimated at 81.1% (Cd),  33.3% (As), 24.1% (Pb of the soil), and 11.8%  (Pb of vegetables). The rate of disappearance is proportional to the distance. At 100m, the  disappearance rate is 100% for As (soil),  96.7% for Cd (soil), 98.6% for Pb in soil, and  88.2% of Pb in vegetables.

Statistical analysis findings a. Kasavubu / Saio Pearson correlation coefficient 

These results are presented in Table 2 below: 

Table 2. Pearson’s correlation coefficient for Kasavubu / Saio 

	pH (KCl)	M.O.	C.O.	Cd/sol	As/sol	Pb/sol	Pb/lég
pH (H2O)	0,86887	0,95795	0,91669	– 0,53556	-0,7906	-0,9118	-0,90243
pH (KCl)		0,9026	0,94944	– 0,76078	-0,92459	-0,9438	-0,91623
M.O.			0,97608	– 0,57616	-0,85742	-0,94115	-0,96991
C.O.				– 0,64825	-0,9249	-0,95793	-0,95632
Cd/soil					0,83958	0,77057	0,6536
As/soil						0,96173	0,87519
Pb/soil							0,92393

Table 2 indicates that there is a negative correlation between the physicochemical parameters and the trace metals under study. In contrast, lead from soil and lead from vegetables show a strong correlation (0.92393). 

a. Pearson correlation coefficient of water 

These results are presented in Table 3 below: 

Table 3. Pearson correlation coefficient of water 

	Water Cd	Water As	Water Pb
Water Cd	1	-0,40203	0,15445
Water As		1	0,06212
Water Pb			1

Table 3 indicates that there is a weak  correlation between trace metals in water  

DISCUSSIONS 

The pH of water wells varies between 5.57  and 6.74, with values less than 6.8; therefore,  slightly acidic but favorable to aquatic life (5- 9.0) and consistent with the pH of groundwater. wells, linked to the same geochemical origin.  So, they don’t have the same origin. 

The dissolved oxygen values of these wells vary between 2.51 and 5.58mg O2 / L. They are lower than those of domestic  Maghrebian waters (2.42 mg / L) and lower than the guideline values for physical,  chemical, and thorough treatment (> 30 mg /  L) (Drouart et al., 1999). This indicates the presence of microorganisms in these wells.  They are also lower than those of the surface water of the Lukaya River (6.7-6.94 mg / L),  almost equivalent to that of groundwater where only fish and insects can live (Ngadi et al., 2014). 

The soil pH in the soil-H2O suspension varies increasingly from 5.12 to 7.3 during the two seasons with average values varying between 5. 1 to 7. 0. This pH, whose standard error bar stands out at 50 m from the initial value of 3 m, shows that the soil is weakly acidic (6.8). The soil is, therefore, suitable for vegetable crops because the plants assimilate the nutrients soluble in water at this pH. It appears that after 50 m from the road, the pH meets the standards required for topsoil. But, at a distance of fewer than  50 m from the roadways, the soil is acidic.  This is due to exhaust gases like CO2, NOX,  SOX, etc. These gases dissolve in water,  forming corresponding acids with an impact on crops, as the acidic pH increases the  Phyto-availability of metals. 

The pH (KCl) is a weak acid (<5.6) from 3 to  100 m, due to the abundant captions released by the complex composing of the soil with a tendency to form acid salts, such as aluminum or silicon and others that combine with the soil and thus form absorbent complexes. The pH thus found with KCl as a solvent is called the actual potential pH of the soil. Average pH – KCl values range from 4.4 to 5.7. Although its value at 20m differs from its initial value at  3m, it is not useful for characterizing market gardening soil. 

Concentrations of organic substances increase with increasing distance from the road. These values vary from 1.0 to 6.9 %  during the two seasons with average values oscillating between 1.1 to 5.7 %. At 30 m, its average value differs from that of 3 m and becomes acceptable for market gardening.  Exhaust fumes have almost a negative impact on organic matter, indicative of the organic carbon needed by the plant. These results  

are consistent with those of cultivated agricultural soil from Saarbrucken in  Germany (1 to 3 %) (Schwartz, 2013). Varying increasingly with the distance from the road, the total organic carbon ranges from 0.15 to 4% during the two seasons, with average values ranging from 0.1 to 3.2% with a value of 1.3 % differing from the initial value.

The presence of proteins,  polysaccharides, and humic compounds from untreated waste is used to amend the soil and is indicative of organic pollution  (presence of carbon), as well as sunburnt substances from gasoline combustion,  including benzene, toluene, and others. They also influence the bioavailability of metals such as cadmium and arsenic. The more organic the soil is, the less the metals will tend to go into solution. The results obtained are lower than those of market gardeners from Loraine in France, whose values exceed  4% (Schwartz, Op. cit.). 

The average values of lead in the soil vary decreasingly, whether it is from Kasavubu or  Saio, during the rainy or dry season. Its average values vary between 2.5 to 0.1 mg/kg. These values are lower than those for  Tshamalenga garden soil (530 mg/kg) (Banza,  2002) and even the guide values (100 mg/kg)  for market gardening soil (Kabata-Pendias et  al. 2001; Boukhars et al., 2000 and Tremel Schaub et al., 2005), and those Polish market garden soil near road traffic, between 3.41  and 1520 mg/kg (Ademe, 2017).

These values are close to those of the market garden soils of  Abidjan (3 mg/kg) and lower than the soils of  Ebrié, 0.12 mg/kg (Vandjiguila et al., 2012)  and higher than the soils of Ezazou village in Cote d’Ivoire (4.9 mg/kg), (Nguelieu, 2017). Lead in the soil forms compounds which are insoluble in water at pH> 5 and also, its leaching and deep contamination are less at this pH. 

In vegetables, the level of lead decreases with increasing distance. Its average values vary respectively between 1.65 to 0.0 mg/ kg.  The change in the lead is inversely proportional to the distance from the road.  Airborne contamination is the main source of lead contamination of vegetables from exhaust fumes. The lead values in the leaves of Amaranthus hybrithus obtained are lower than those obtained by the influence of phytosanitary products 4 mg/kg. This shows that vegetables grown under conditions of strong anthropogenic contamination contain high amounts of trace elements including lead (Schwartz et al., 2000). 

The values obtained are lower than those of  Lubumbashi near the mining areas (3.1  mg/kg) in Tshamalenga and Shinkolobwe  (5.352 mg/Kg) (Banza, 2002). These values are beyond the thresholds required for human consumption in accordance with  European standards, 2011 (0.1 mg/kg) cited by OPALA (2017) and those described by  Banza (Op.cit).

Similar work carried out in the market gardening perimeters located along the heavily trafficked roads in Kinshasa by  Musibono (2003) reported that the vegetables grown on these sites are polluted by the lead contained in the smoke released by the vehicles itself coming from gasoline-containing tetraethyl lead. He further noted that the lead content in both soil and vegetables decreases with increasing distance from the main pathways. 

Lead values in vegetables are lower than those in soils and water. All lead values in well water vary between 0.4-2.4 mg/L. These concentrations are higher compared to the limit values (0.2 mg/L) for discharges into aqueous tributaries and the guide values  (0.01 mg/L), WHO, 2004. And these concentrations are lower compared to the values defined for irrigation water (5.0 mg/L),  (Fatta, Op. cit).  

The lead transfer factor from soil to vegetables varies from 0.6 to 5.7, falling within the range set values (0.01 and 10)  (Tangou, 2016). Only the value from 50m  from the roadways reveals the transfer of soil to the plant because the transfer factor F  (5.7) is greater than 5.6. Unlike those of  

Arsenic and Cadmium, where no transfer is possible because factor F is almost zero.  Therefore, at this pH, the availability of Cd and as for plants is not possible. According to  Bourg and Lock (1995), Cd forms chelate complexes and its absorption becomes independent of pH (Babich et al., 1977). 

The cadmium concentration decreases significantly from 5m from the road and stabilizes thereafter. The average cadmium level varies between 0.5 to 0.0 mg/kg. At  5m, it stands out from the value at 3m from the road. These values are greater than 3 m  (0.9 mg/kg rainy season and 1.0 mg/kg dry season) of the road than those of arable soil  (0.7 mg/kg) (Rousseau 1986 cited by Kabata Péndias et al., 2001) and to the reference values applicable in Wallonia according to the Flemish regional regulations on the matter (0.2 mg/kg), AFNOR, 2005 cited by  Nguelieu (2017), lower than the latter from  5m (0.17 at 0.03 mg/kg), and the French standard for agricultural soil (2 mg/kg).

These values are lower than that of Tshamalenga garden soil (1.45mg/kg) (Banza, 2002) and even the guide values (2 mg/kg) for market gardening soil (Kabata-Pendias et al., 2001,  Boukhars et al., 2000 and Tremel-Schaub et al., 2005). This situation is due to tire wear at the edges of the main roads but does not affect the entire garden. The Cadmium transfer factor from the soil to the vegetables is zero. 

Only wells P6 to P8 (0.7-0.9mg/L) have  Cadmium values beyond WHO standards for human consumption (0.03 mg/L) (WHO,  2004). Values higher than those predicted for irrigation water (0.01mg/L), Fatta, (2014) and the limit values for discharges into aqueous tributaries (0.05 mg/L) (Lepot et al., 2013).  But these values did not influence the Cd of vegetables analyzed. 

Arsenic concentrations decrease less with distance from the road; its average values vary from 0.08 to 0.00 mg/kg. An almost low value in the soil compared to the soil of  Tshamalenga (10 mg/kg) Banza, 2002.

The arsenic values of well water are higher than those predicted for surface water  (Vandjiguila et al., 2012), for irrigation water  (0.1 mg /L) (Fatta, 2014), and the limits of the value (1 mg/L) for discharges into aqueous tributaries (Lepot et al., 2013). 

The Student’s T of the parameters analyzed showed that whether it is in Kasavubu or  Saio, rainy or dry season, the difference is not significant. The values found are averages of these parameters. 

The Student’s T of the parameters analyzed showed that whether it is in Kasavubu or  Saio, rainy or dry season, the difference is not significant. The values found are averages of these parameters. 

Pearson’s coefficient was applied between physicochemical parameters and trace metals. From this correlation came the  following result: 

There is an inverse correlation between the trace metals and the physicochemical parameters (pH, Organic matter, and Total organic carbon), i.e. the more the trace metals decrease, the more the physicochemical parameters increase as indicated in Figure 15 below. These parameters influence the trace metals in soils. 

Lead, Cadmium, and Arsenic in soil have a  very weak correlation, so they do not have the same source of contamination. This weak correlation can be linked to the same geochemical source. Lead in soil has a strong correlation with that in leafy vegetables, so they have the same source of contamination,  which comes from anthropogenic sources including exhaust smoke from motor vehicles.

Leaching is the main cause of the difference in concentration between lead in soil and that in vegetables; this corroborates the results of Neibor et al., 1980, who found a correlation between the lead content in soil and that in plants. The trace metals (Pb, Cd, and As) in the water from different wells used for irrigation are not correlated and therefore do not have the same origin. 

CONCLUSION 

The main objective of the study was to assess the level of contamination of Amaranthus hybridus with toxic metallic trace elements including Pb, Cd, and As in order to deduce the safe culture distance or the useful area.  Results obtained show that the average level of lead in the soil decreases with distance from the road in all seasons. It ranges from  2.5 to 0.1 mg/kg. In vegetables, the average level of lead decreases with increasing distance. It ranges from 1.65 to 0.00 mg/kg.  In addition, lead is more concentrated in green vegetables than in the sauce of cooked vegetables. The lead transfer factor from soil to vegetables varies from 0.6 (3 m) to 5.7  (50m). 

The average level of Cadmium in the soil between 3 and 10 m decreases with distance from the road in all seasons. It ranges from  0.5 to 0.00 mg/kg. The Cadmium transfer factor from the soil to the vegetables is zero.  The cadmium level is higher in wells 6 (P6)  and 12 (P12) and low in wells 3 (P3). Its value  is zero in wells 9 (P9) 

The average level of Arsenic in the soil decreases a bit with the distance from the  Kasavubu and Saio roads. It ranges from 0.1  to 0.00 mg/kg. The arsenic transfer factor  from soil to vegetables is zero 

Point 0 of these toxic elements is located around 50m from the road. The decrease in these elements is observed relative to the molecular weight of each. The heaviest finish their race at an intermediate distance and the lightest reaches 40-50m. This disappearance also depends on the initial concentration. The disappearance of lead was observed from 40-45m. 

The useful area for healthy market gardening is estimated at 50m from the roadway. At this distance, more than 80% of the metallic trace elements (TME) disappeared during the process. The transfer factor of the lead concentration from the soil to the vegetables is estimated at 5.7 because the pH is 7.09  favoring mobility. 

We recommend to the municipal authority a  strict ban on vegetable cultivation within  50m of high-frequency motorized roads to protect the population against carcinogenic contaminants. 

REFERENCES 

Abderrazzak, A. B. Etude de contamination et  d’accumulation de quelques métaux lours  dans les céréales, légumes et sols agricoles  irrigués par les eaux usées de la ville de  Hammam Boughrana, Ph.D. dissertation,  Abou BekrBelkaid-Tlemen University,  Algeria, 2012. 

Ademe. Phytodisponibilité des ETM sur les  plantes potagères et extrapolation dans la  quantification d’exposition des  consommateurs, University of Lorraine,  France, 2017.  (www.ademe.fr/médiathèque). 

Ancelle, A. ; Statistique épidémiologie,  Fundamental Sciences Collection, 2^nd Ed.,  Maloine, 2008. 

Atidegla, S. C.; Agbossou, E. K. ; Huat, J.; Kakai  R. G. Contamination métallique des  légumes des périmètres maraîchers  urbains et péri urbains: Case of the  municipality of Grand – Popo in Benin. Int.  J. Biol. Chem. Sci. 2011, 5(6), 2351-2361. 

Aubry, C.; Dabat, M. H.; Mawois, M. Fonction  Alimentaire de l’agriculture urbaine au  Nord et au Sud: Permanence et  renouvellement des questions de  recherche. ISDA 2010, Jun 2010,  Montpellier, France. 13 p. 2010, Hal 00521221. 

Babich, H.; Stotzky, G. Sensitivity of Various  Bacteria, including Actinomycetes and  Fundi to Cadmium and Influence of pH on  Sensitivity appl. Environ. Microbiol. 1977, 681-685. 

Banza, C. Investigation report on chemical pollution in the Tshamalenga and Kabecha districts of the city of Lubumbashi, ESP,  Toxicological Unit, University of  Lubumbashi, Fac. Medicine, 2002, 56 p. 

Baize, D. Teneurs totales en éléments traces  métalliques dans les sols, France: INRA  edition, 1997, 408 p. 

Barriuso, E.; Calvet, R.; Schiavon, M.; Soulas  G. Les pesticides et les polluants  organiques des sols. Transformation et  dissipation. Forum « Sol, un patrimoine  menacé ? Etude et Gestion des Sols,1996, 3 (4), 279-295. Paris Special issue. 

Boukhars, L. ; Rada A. Exposition au cadmium  de végétaux cultivés sur des sols calcaires  salés marocains amendés avec des boues  et des eaux usées, Environ. Technol. 2000,  21, 641-652. 

Bricas, N. ; Seck, P. A. L’alimentation des  villes du Sud : les raisons de craindre et  d’espérer, Cahiers Agriculture, n° 13, 10-14 pp. 

Clinard, F. ; Delefortrie, A. ; Bellec, S.; Jacquot, G. ; Bonnelles, A. ; Tillier, C. ; Richert, J. Enquête de pratiques agricoles et  de consommation alimentaire dans les jardins ouvriers de l’agglomération de  Belfort (Franche-Comté). Environment risks  & health, 2015, 14 (1), 56-71. 

Deletraz, G. Géographie des risques  environnementaux liés aux transports  routiers en montagne. Incidences des  émissions d’oxydes d’azote en vallées  dʼAspe et de Biriatou (Pyrénées). “Ph.D. Dissertation in Geography-Planning”.  University of Pau and the Adour countries.  Institute for Research on Societies and  Planning. 2002, 564 p. 

Dubbeling, M. L’intégration de l’agriculture  urbaine dans la planification urbaine,  Exposé à la Table Ronde sur l’agriculture  Urbaine, Institute of Trades of the City and  Urban Municipality of Antananarivo, 2009,  4-9 / 9/09. 

Dumat, C. ; Xiong, T. Shahid, M. Agriculture  urbaine durable : opportunité pourla  transition écologique. European University  Press, Saarbrücken, 2016, DE. ISBN 978-3- 639-69662-2. 

Drouart, E. and Vouillamoz, J.M.;  Alimentation en eau potable des  populations menacées, Paris: ACT, Hermat  Editions, 1999. 

Fatta D.; Department of Civil and environment engineering, University of  Cyprus, 2014. 

FAO, L’agriculture biologique peut contribuer  à la lutte contre la faim, FAO, Relation  media, Rome. 3 p,  www.fao.org/newsroom/fr/news/2007. 

Flouriot, J.; Croissance de l’habitat, in  Flouriot, J., De Maximi, R., Pain, M. (Dir.),  Atlas de Kinshasa, Kinshasa: National  Geographic Institute, 1975. 

Hanane, B., Benchaben, H., Nadira A.  Abbassia A.; Quantification de l’émission  de plomb dans le milieu urbain de Sidi Bel’  Abbes (Algérie occidentale) Europ. Scient. J.  February 2015 edition vol.11, No.6: 82-94  ISSN: 1857 – 7881 (Print) e – ISSN 1857- 7431. 

Kabata-Pendias, A., Trace Elements in Soils and Plants, (3^rd Ed.). USA: CRC Press, Boca  Raton, 2001.413p. 

Kalavrouziotis, I.K., Carter, J., Varnavas, S.P.,  Mehra, A., Drakatos P.A.; Towards an understanding of the effect of road pollution on adjacent food crops: Zea mays as an example. Int. J. of Environ. and Pol.,  2007, 30:576-592. 

Lelo, N. F. Kinshasa, ville et environnement,  Paris: L’Harmattan, 2008. 

Lepot, B. and Poulleau J.; Méthodes de mesurage des polluants rejetés dans  l’atmosphère et dans l’eau, Final report, INERIS, 2013, 549p. 

Leveque, T., Capowiez, Y., Schreck, E.,  Mombo, S., Mazzia C., Foucault, Y. &  Dumat, C.; Effects of historic metal(loid)  pollution on earthworm communities.  Science of the Total Environment, 2015, 511, 738-746. 

Menkes, D.B. et Fawcett JP. ; Too Easily Lead?  Health effects of gasoline additives. Environ  Heulth Perspective, 1997, 105: 270-273. 

Mougeot, L.J.A.; Agropolis: The Social,  Political and Environmental Dimensions of  Urban Agriculture. IDRC, Earthscan,  London, 2005, 286 p. 

Musibono, D. ; Pollution au plomb des  légumes cultivés le long des artères  publiques à Kinshasa, INRB. Scientific  Department, Conference report published  by mail to the readers, 2003, 4p.  www.lettres@digitalcongo.net, (accessed  June 15, 2018). 

Musibono, D. E.; Biey, E., Kisangala, M.,  Nsimanda, C., Munzundu, B., Kekolemba,  V. & Paulus, J.; Urban agriculture as a  response to unemployment in Kinshasa,  Democratic Republic of Congo. [Vertigo]  The electronic journal of Environmental Sciences, 2011,11 (1). [Online], Volume 11  Number 1 | May 2011, posted May 20,  2011, URL:  http://vertigo.revues.org/10818; DOI:  10.4000 / vertigo.10818, (accessed June  15, 2018). 

Ngadi, R., Idrissa A. and Pongi J.; Impact de  rejet fiente de la ferme Minocongo sur la  variation saisonnière des paramètres  physicochimiques des eaux brutes de la  rivière Lukaya. CRIDUPN review, October – December 2014, n ° 61C. 

Nguelieu, C.R.; Evaluation des risques de  contamination en éléments traces (Pb, Cd,  Zn) des sites maraichers urbains de  Yaoundé, University of Liège, Master in  Agro-Biotechnology, 2017, 59p.  (http://lib.ulg.ac.be), (accessed September  12, 2018). 

Nieboer, E. et Richardson, D.; The  Replacement of the descript term “Heavy  Metals” with biologically and chemically significant classification of metal ions, J.  Environ Pollution, 1980, 3-26. 

WHO; Directives de qualité pour l’eau de  boisson; (3^rd.Ed.), (2004). Opala, C. Impact du trafic routier sur les  activités maraichères à Kinshasa, Master  Dissertation, UNIKIN, 2017. 

Pagotto, C.; Etude sur l’émission et le  transfert dans les eaux et les sols des  éléments traces métallique et des  hydrocarbures en domaine routier. Ph.D.  Dissertation: water chemistry and  microbiology, science and technology.  University of Poitiers, 1999, 252 p. 

Rhue, R. D.; Mansell, R. S.; Oult Cox, R.; Tang  S. R.; etOuyang, Y. The fate and behavior of  lead alkyls in the environment: a review.  Crit Rev Environ Control. 1992, 22, 169-193. 

Shahid, M.; Dumat, C.; Khalid, S.; Niazi, N.; Antunes, P. M. C. Cadmium Bioavailability,  Uptake, Toxicity and Detoxification in Soil Plant System. 2016, Springer, New York. 

Schreck, E.; Dappe, V.; Sarret, G.; Sobanska, S.; Nowak, D.; Nowak, J.; Stefaniak, E. A.; Magnin, V.; Ranieri, V.; Dumat, C. Foliar or root exposures to smelter particles:  consequences on lead compartmentalization and speciation in plant leaves. Science of The Total  Environment, 2014, (476–477), 667–676. 

Schwartz, C. Les sols de jardins supports  d’une agriculture urbaine intensive, Vertigo, Special issue 15, Atmospheric  pollution, transport and agriculture, 2013. 

Tangou, T. Chimie Environnement, pollutions  et nuisances, Ed. P.U.K., University of  Kinshasa, 2016, 139 pp. 

Tremel-Schaub, A.; Feix, I. Contamination des  sols – Transferts des sols vers les plantes,  EDP Sciences, ADEME, 2005, 416 pp. 

Uzu, G.; Schreck, E.; Xiong, T.; Macouin, M.; Lévêque, T.; Fayomi, B.; Dumat, C. Urban market gardening in Africa: metal (oid)  foliar uptake and their bioaccessibility in vegetables, implications in terms of health risks. Water, Air & Soil Pollution, 2014, 225, 2185. 

Vandjiguila, D. ; Darby, V. Problématique du  Cd en Côte-d’Ivoire : Pollution  environnementale et risque sanitaire,  Article, Institut Pasteur de Cote d´Ivoire, Félix Houphouët Boigny University, Cote  d´Ivoire, 2012. 

Wekolo, E. Contamination métalliques des  légumes des périmètres maraichers de  Kinshasa, cas des sites Camp Kokolo et Saio,  a Graduate Research paper, Fac. Sciences,  UNIKIN. 2018. 

Wagemakers, I. ; Makangu, O. D. De Herdt, T.  Lutte foncière dans la ville : gouvernance  de la terre agricole urbaine à Kinshasa  l’Afrique des Grands Lacs. 176 yearbooks  2009-2010, 175-200. 

Wieczorek, J.; Wieczorek, Z.; Bieniaszewski T.  Cadmium and lead content in cereal grains and soil from cropland adjacent to roadways. Polish J. of Environ. Stud. 2005.  14, 535-540. 

Xiong, T.; Austruy, A.; Pierart, .A.; Shahid M.; Schreck, E.; Mombo, S.; Dumat, C. Kinetic study of phytotoxicity induced by foliar lead uptake for vegetables exposed to fine particles and implications for sustainable urban agriculture. Journal of Environmental  Sciences. 2016.