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. 2015 Jun 25;3(6):604–611. doi: 10.1002/fsn3.252

Effect of brick kiln emissions on commonly used vegetables of Kashmir Valley

Bhat M Skinder 1,✉, Afeefa Q Sheikh 1, Ashok K Pandit 1, Bashir A Ganai 1, Aashiq H Kuchy 1
PMCID: PMC4708652  PMID: 26788302

Abstract

To study the impact of brick kiln emissions on plant growth and productivity, a study was conducted on various biochemical parameters of three main vegetables Brassica oleracea L., Phaseolus vulgaris L., and Solanum melongena L. cultivated in the vicinity of the brick kiln area of the Panzan village of district Budgam (J&K). Plants in the vicinity of brick kilns are direct recipients of emissions and therefore important materials for assessing potential effects of kiln pollutants. The biochemical values of all the three vegetables of the brick kiln site when compared to the control site are significantly (P ≤ 0.05) different. The findings of the present work depict that the brick kilns are the prime reason for the deterioration of important consumable vegetables, which could lead to chaos in the food security of the area in concern besides a threat to local people in terms of health if proper pollution control devices or the replacement of brick kilns are not put in place with new technology.

Keywords: Biochemical parameters, Brassica oleracea, brick kiln, emissions, Phaseolus vulgaris, Solanum melongena

Introduction

Plants are indispensable part of ecosystems and their sensitivity to air pollution is more considerable than standards of air pollution (Thomas 1991). Air pollution has become a serious environmental stress to crop plants due to increasing industrialization and urbanization during the last few decades (Rajput and Agrawal 2004). Diverse changes induced by different air pollutants in plants with respect to morphological, anatomical and physiological characteristics have been investigated (Rao 1981; Pawar and Dubey 1983; Rao and Dubey 1988). The most dispersed and injurious pollutants in industrial areas (brick kilns) are sulfur dioxide (SO2), nitrogen oxides (NOx), carbon monoxide (CO), tropospheric ozone (O3), and heavy metals, as well as suspended particulate matter (Asgher and Singh, ; Assadi et al. 2011). Estimates indicate that annual emissions from a brick industry were 80 tons of particulate, 30 tons of carbon, 7 tons of NOx, and 5 tons of SOx (Asgher and Singh, 2003). A range of air pollutants is recognized as phytotoxic agents and phytotoxicity of sulfur dioxide has been documented for about a century (Godzik and Sienkiewicz 1990), sound effects of ozone for more than 30 years (Miller 1983), acidic precipitation for more or less 20 years (Likens et al. 1979), and effects of prominent levels of nitrogen compounds, nitrogen oxides, and ammonia in the last decade (Nihlgard, ). The significance of other pollutants such as peroxy acetyl nitrate (PAN) (Su et al. 2006), fluorides (Maclean 1981), or heavy metals have also been documented (Unsworth and Harrison 1985). Plants in the immediate vicinity of emissions sources are more vulnerable. It has been revealed that the most sensitive species of plants start on to show visible signs of damage to sulfur oxides at concentrations of about 1850 μg/m3 for 1 h, 500 μg/m3 for 8 h, and 40 μg/m3 for the maturing season (Smith 1981, cited in NAPAP 1990). Sulfur dioxide shows negative effects in terms of foliar injury, physiological and biochemical alterations on vegetation (Ganai et al. 2007a,b; Balkhi et al. 2009; Irshad et al. 2011), and short‐term treatment of SO2 damaged PSII, decreased the fluidity of thylakoid membrane, and affected the process of electron transport (Liu et al. 2007). The particulates and gaseous pollutants, alone and in combination can cause grave setbacks to the overall physiology of plants (Ashenden and Williams 1980; Mejstrik 1980; Anda 1986). Of all plant parts, the leaf is the most sensitive part to the air pollutants (Singh 1990).

Accumulation of particulates on the surface of the plants can in due course alter plant vulnerability to pathogens and pests (Emberson et al. 2001) and the exposure to dust provoked a significant reduction in photosynthesis in most plants. Thus, may alter plant growth and production, without physical damage to the plant (Kumar and Thambavani 2012). It is now generally accepted that cellular membranes are among the primary sites of pollutant attack and, since lipids are important membrane components and play essential roles in maintaining membrane structure and function, many workers have examined the effects of pollutants on lipids to clarify the mechanisms of their phytotoxicity (Mudd et al. 1984; Sakaki 2002). The fact that plants provide a vast leaf area for impingement, assimilation and accumulation of air pollutants diminish the pollutant level in the air environment (Warren 1973; Shannigrahi et al. 2004), it is reported that depending on their sensitivity level, plants show visible changes which would include alteration in the biochemical processes or accumulation of certain metabolites (Agbaire and Esiefarienrhe 2009), thus can be used as bioindicator of air pollution (Tripathi and Gautam 2007; Lalitha et al. 2013).

Brick kilns are known to be a leading cause of ambient air pollution in rural areas. The levels of SOx, NOx, and SPM are major problems in the Panzan village of district Budgam because the levels of these pollutants are significantly higher than NAAQS guidelines during the operational phase of brick kilns and especially play a significant role in elevating the SO2 concentration in the ambient air, as they are fed with sulfur rich, inferior quality of coal (2.5 to 3.0 tons/season/kiln) besides the use of inefficient and outdated technology such as Bull's Trench kilns (Skinder et al. 2014). High air pollution levels in the atmosphere have shown the significant negative importance, as they do not only pose serious occupational health hazards but also adversely affect the surrounding environment (Guttikunda 2009; Ganai et al. 2010; Pawar et al. 2010).

Considering the facts that air pollutants have damaging effects and shocking consequences on the exposed plants, the present work was designed to estimate the biochemical parameters of the commonly used vegetables of Kashmir (India). The study evaluated the effects of brick kilns on the biochemical parameter and the consequences there upon. Our study highlighted the concern of brick kiln emissions on the quality of local vegetables which is highly a pressing issue among the people living in the study area and other similar populations throughout the globe.

Material and Methods

This study was conducted in the rural area of district Budgam in Kashmir valley at Panzan village, where mushrooming of brick kilns is a serious threat to air quality and consequently to vegetation. For the plant analysis, the fresh leaves of three available vegetables were used as study material and were collected from two sites, that is, brick kiln site (Site I) (app. 50 m away, 33°57′56.51″N and 74°46′19.06″E) and the other site with similar ecological conditions was selected as the control (least polluted) Site II (app. 2–4 km away, 33°58′38.66″N and 74°48′43.33″E) throughout the growing season over a period of 3 months from July 2012 to September 2012 during the operational phase of brick kilns. The leaf samples were immediately taken to the laboratory for analysis.

Biochemical analysis

Fresh leaves of the vegetables were used as study material and were collected from two sites, that is, brick kiln site (S I) and control site (S II). The samples of plant species were collected in replicates, placed in airtight polyethylene bags separately and carried to the laboratory for further analysis. The material was washed thoroughly and moisture was drained before analysis for various biochemical contents. The analysis was done as per standard methods:

Estimation of total protein

The protein content of vegetable leaves was determined colorimetrically by the method of Lowry et al. (1951) after the extraction of proteins with buffer solution of pH‐7.

One gram (1 g) of fresh weight of plant material was homogenized by grinding with buffer solution of pH‐7 using mortar and pestle. About 0.2 mL and 0.4 mL of the extract were pipetted into two separate test tubes and 5 mL of freshly prepared alkaline copper tartrate reagent was added, followed by 0.5 mL of IN Folin's reagent to each test tube. The contents of each test tube were immediately vortexed and subsequently incubated for 30 min at room temperature for color development. The absorbance was then read at 700 nm against a reagent blank using visible spectrophotometer. Bovine serum albumin was used as standard and the results were expressed as mg% of fresh weight of leaves.

Estimation of total carbohydrates

The carbohydrate content of vegetables was determined colorimetrically by phenol–sulfuric acid method after extraction into the buffer solution of pH 7 (Dubois et al., 1951).

One gram (1 g) of fresh weight of plant material was homogenized with buffer solution of pH‐7 using mortar and pestle. About 0.5 mL and 1 mL of the extract were pipetted into separate test tubes and 1 mL of 5% phenol was added followed by rapid addition of 5 mL of conc. H2SO4. The contents were shaken thoroughly and subsequently incubated for 40 min at room temperature for color development. The absorbance was then measured at 490 nm against a reagent blank using visible spectrophotometer. Glucose was used as standard and the results were expressed as mg% of fresh weight of leaves.

Estimation of total lipids

The total lipid content of the vegetables was determined colorimetrically by Sulphophosphovanillin method after extraction in buffer solution of pH‐7 (Knight et al. 1972).

One gram (1 g) of fresh weight of plant material was homogenized with buffer solution of pH‐7 in pestle mortar and 0.1 mL of the extract was pipetted in a separate test tube and digested with 2 mL of conc. H2SO4. After cooling the test tube, 5 mL of Phosphovanillin reagent was added and the sample was subsequently incubated for 40 min at room temperature for color development. The absorbance was then measured at 540 nm against a reagent blank using visible spectrophotometer. Olive oil was used as standard and the concentration of total lipid was calculated by using the following formula.

Calculation:

(AT−AB)/(AS−AB)×500,

where A T = Absorbance of test sample; A B = Absorbance of blank; A S = Absorbance of standard. The results were expressed as mg percentage of fresh weight of vegetables leaves.

Estimation of photosynthetic pigments chlorophyll, phaeophytin, and carotenoids content in photosynthetic tissue (leaf)

The method of plant pigment isolation and estimation from green plant leaves is based on the principle of extraction of loosely protein‐bound pigments by the help of organic solvents such as acetone and measuring their color intensity in visible region by Spectrophotometric method.

One gram (1 g) of fresh weight of the main chlorophyll‐bearing organ of the plant species was extracted with 80% aqueous acetone by macerating the samples using a mortar and pestle. The decanted suspension was centrifuged for 3 min at 195 g. After centrifugation, the upper green clear solution was decanted from the colorless residue and then made up to 10 mL with 80% acetone in 10 mL test tubes. The material was then subjected to centrifugation at 11200 g for 10 min. The optical density (O.D) of the solution was determined using a spectrophotometer at different wavelengths like 665 nm, 649 nm, 666 nm, 510 nm, and 480 nm, respectively. The results were expressed as μg/mL of fresh weight of plant sample.

  1. The chlorophyll content was measured according to Strain et al. 1971

    Chlorophyll a (μg/mL) = 11.63 (O.D.665) – 2.39 (O.D.649)

    Chlorophyll b (μg/mL) = 20.11 (O.D.649) – 5.15 (O.D.665)

    Total Chlorophyll (μg/mL) = 6.45 (O.D.665) + 17.72 (O.D.649)

  2. The phaeophytin content was estimated according to Vernon (1960)

    Phaeophytin a (μg/mL) = 20.15 (O.D.666) – 5.87 (O.D.665)

    Phaeophytin b (μg/mL) = 31.96 (O.D.665) – 13.65 (O.D.666)

    Total phaeophytin (μg/mL) = 6.75 (O.D.666) + 26.03 (O.D.665)

  3. The carotenoids content was estimated according to method of Duxbury and Yentsch (1956)

    Carotenoids (μg/mL) = 7.6 (O.D.480) – 1.49 (O.D.510)

Statistical analysis

All experiments were performed in triplicates. Statistical analysis were performed using Statistical Package for Social Sciences (SPSS 16.0) software for Windows with a significance level of alpha = 0.05. One‐way ANOVA and the Duncan's new multiple range test (Sokal and Rohlf 1981) was used to compare the means as well as the seasonal differences in various parameters in control and also in the vegetable leaves affected by brick kiln emissions.

Results and Discussion

The data collected for two sites (Site I and Site II), were compared to find out the impact of brick kiln emissions on plant productivity. Brassica oleracea (locally called Saagh) showed a general decrease in respect of total chlorophyll, total phaeophytin, carotenoids, protein, carbohydrate, and lipids as the exposure level of pollutants increases in due course of time at the brick kiln site (Site I) till it touched the lowest (74.36%, 74.27, 51.99, 55.85, 53.12, and 28.31%, respectively, in all parameters) in the month of September (Table 1).

Table 1.

Impact of brick kiln emissions on biochemical parameters of Brassica oleracea L.

Parameters July August September
S‐II (Control) S‐I %D S‐II (Control) S‐I %D S‐II (Control) S‐I %D
Chlorophyll ‘a’ (μg/mL) 22.68 ± 0.90d 17.33 ± 0.64c 23.59 22.14 ± 1.32d 11.35 ± 1.85b 48.75 20.75 ± 1.61d 5.66 ± 0.16a 72.70
Chlorophyll ‘b’ (μg/mL) 18.08 ± 3.04d 12.10 ± 2.46bc 33.10 13.11 ± 1.17bc 9.55 ± 2.59b 27.16 14.50 ± 0.7c 3.37 ± 0.15a 76.73
Total Chlorophyll (μg/mL) 40.76 ± 2.23e 29.42 ± 3.09c 27.81 35.25 ± 2.48d 20.90 ± 2.10b 40.72 35.25 ± 1.00d 9.04 ± 0.13a 74.36
Phaeophytin ‘a’ (μg/mL) 29.65 ± 3.8d 21.16 ± 2.00c 28.65 27.31 ± 2.47d 14.50 ± 1.22b 46.88 25.97 ± 0.7d 4.53 ± 0.15a 82.55
Phaeophytin ‘b’ (μg/mL) 42.99 ± 1.75d 33.34 ± 3.71c 22.44 41.71 ± 3.42d 21.89 ± 4.06b 47.53 39.49 ± 4.35d 12.34 ± 0.38a 68.75
Total Phaeophytin (μg/mL) 73.04 ± 2.58e 54.78 ± 1.70c 24.99 69.39 ± 4.10de 36.59 ± 4.43b 47.27 65.81 ± 3.66d 16.93 ± 0.38a 74.27
Carotenoids (μg/mL) 14.13 ± 0.45e 11.42 ± 1.50c 19.22 13.51 ± 0.91de 8.91 ± 0.24b 34.04 12.14 ± 0.33cd 5.83 ± 0.34a 51.99
Proteins mg% 41.78 ± 3.97de 38.89 ± 4.20cd 6.94 45.94 ± 4.81e 31.28 ± 2.58b 31.92 47.03 ± 4.30e 20.77 ± 1.41a 55.85
Carbohydrates mg% 60.15 ± 4.71c 57.64 ± 4.76c 4.18 63.85 ± 3.15c 43.95 ± 4.12b 28.79 67.05 ± 3.09d 31.44 ± 3.62a 53.12
Lipids mg% 10.81 ± 0.76bc 9.45 ± 0.83a 12.62 12.01 ± 1.00c 9.80 ± 0.72ab 18.43 15.34 ± 0.85d 11.00 ± 0.49bc 28.31
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Data represent the mean of three replicates analyzed separately ±standard deviation values and %D = percent of decrease; Values with different superscripts in rows are significantly (P ≤ 0.05) different.

A similar trend was maintained by other two vegetables (Phaseolus vulgaris L. and Solanum melongena L.) with increasing level of exposure of pollutants at the brick kiln site (Site I). The highest decrease in investigated biochemical parameters like total chlorophyll, total phaeophytin, carotenoids, protein, carbohydrate, and lipids was observed in the month of September again. However, there were some remarkable differences in the levels of said parameters of the vegetables. In case of Phaseolus vulgaris L., the decreased percent were 61.37, 55.30, 55.58, 64.58, 68.59, and 14.26% in the respective biochemical parameters when compared to the control site (Site II) (Table 2). While as, in case of Solanum melongena the decreased levels were 60.56, 49.18, 28.78, 63.66, 60.99, and 11.94% for total chlorophyll, total phaeophytin, carotenoids, protein, carbohydrate, and lipids, respectively, for Site I as compared to the control Site II (Table 3).

Table 2.

Impact of brick kiln emissions on biochemical parameters of Phaseolus vulgaris L.

Parameters July August September
S‐II (Control) S‐I %D S‐II (Control) S‐I %D S‐II (Control) S‐I %D
Chlorophyll ‘a’ (μg/mL) 24.35 ± 0.33d 19.50 ± 0.67c 19.92 23.69 ± 0.50d 14.82 ± 1.38b 37.45 20.60 ± 0.53c 10.06 ± 0.62a 51.17
Chlorophyll ‘b’ (μg/mL) 20.20 ± 0.55e 16.70 ± 1.35cd 17.31 17.85 ± 0.87d 8.49 ± 0.54b 52.44 14.93 ± 2.43c 3.67 ± 0.15a 75.44
Total Chlorophyll (μg/mL) 44.55 ± 0.70e 36.20 ± 1.44c 18.74 41.54 ± 1.14d 23.31 ± 0.89b 43.89 35.52 ± 2.75c 13.72 ± 0.71a 61.37
Phaeophytin ‘a’ (μg/mL) 32.96 ± 0.65d 22.34 ± 2.81b 32.23 30.61 ± 0.27cd 19.99 ± 0.51b 34.69 28.88 ± 2.02c 9.16 ± 1.45a 68.29
Phaeophytin ‘b’ (μg/mL) 45.63 ± 1.17d 39.45 ± 3.02c 13.55 44.85 ± 1.50d 26.67 ± 3.70b 40.53 37.27 ± 1.91c 20.46 ± 2.37a 45.12
Total Phaeophytin (μg/mL) 79.02 ± 0.82e 62.08 ± 1.57c 21.44 75.87 ± 1.33e 46.93 ± 3.19b 38.15 66.53 ± 2.17d 29.74 ± 1.32a 55.30
Carotenoids (μg/mL) 14.18 ± 0.17c 11.95 ± 0.46b 15.76 12.14 ± 0.50b 5.57 ± 0.39a 54.09 14.13 ± 0.75c 6.28 ± 0.34a 55.58
Proteins (mg %) 49.83 ± 2.92c 50.91 ± 3.05d −2.17 57.01 ± 3.61e 31.02 ± 2.95b 45.60 63.89 ± 3.46e 22.63 ± 3.51a 64.58
Carbohydrates (mg %) 62.99 ± 2.54c 58.47 ± 2.96c 7.17 71.89 ± 4.16d 50.00 ± 3.73b 30.44 73.92 ± 4.31d 23.22 ± 3.10a 68.59
Lipids (mg %) 68.59 ± 3.91ab 65.86 ± 4.35a 3.98 72.16 ± 3.25bc 68.71 ± 3.26ab 4.79 84.27 ± 2.48d 72.25 ± 3.03c 14.26
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Data represent the mean of three replicates analyzed separately ±standard deviation values and %D = percent of decrease; Values with different superscripts in rows are significantly (P ≤ 0.05) different.

Table 3.

Impact of brick kiln emissions on biochemical parameters of Solanum melongena L.

Parameters July August September
S‐II (Control) S‐I %D S‐II (Control) S‐I %D S‐II (Control) S‐I %D
Chlorophyll ‘a’ (μg/mL) 21.74 ± 1.56d 20.60 ± 2.01d 5.24 24.57 ± 0.99e 12.56 ± 1.96b 48.88 17.60 ± 0.42c 9.20 ± 1.24a 47.73
Chlorophyll ‘b’ (μg/mL) 13.10 ± 4.55bc 11.37 ± 0.70b 13.19 17.58 ± 2.75d 9.59 ± 0.76b 45.44 15.65 ± 1.24cd 3.92 ± 0.84a 74.99
Total Chlorophyll (μg/mL) 34.84 ± 6.04c 31.98 ± 2.17c 8.23 42.15 ± 3.70d 22.15 ± 1.21b 47.45 33.25 ± 0.94c 13.11 ± 0.89a 60.56
Phaeophytin ‘a’ (μg/mL) 29.19 ± 2.20d 23.82 ± 3.20c 18.39 34.09 ± 2.15e 17.09 ± 2.72b 49.85 20.53 ± 1.42bc 12.14 ± 1.38a 40.86
Phaeophytin ‘b’ (μg/mL) 39.42 ± 5.24cd 39.64 ± 3.05cd −0.57 44.63 ± 1.89d 23.22 ± 2.91b 47.97 35.53 ± 0.70c 16.33 ± 2.04a 54.05
Total Phaeophytin (μg/mL) 69.00 ± 5.45d 63.79 ± 6.19cd 7.56 79.17 ± 4.01e 40.54 ± 5.66b 48.79 56.34 ± 1.19c 28.63 ± 3.44a 49.18
Carotenoids (μg/mL) 19.16 ± 1.78c 15.80 ± 1.59b 17.54 20.97 ± 2.31c 13.39 ± 0.08ab 36.16 15.96 ± 0.87b 11.36 ± 1.82a 28.78
Proteins (mg %) 77.65 ± 2.40d 65.49 ± 3.93c 15.66 84.50 ± 4.07e 48.04 ± 2.64b 43.15 85.12 ± 4.63e 30.93 ± 2.57a 63.66
Carbohydrates (mg %) 61.72 ± 3.60c 59.89 ± 2.48c 2.97 65.89 ± 5.10c 49.38 ± 3.85b 25.06 71.83 ± 4.29d 28.02 ± 2.18a 60.99
Lipids (mg %) 161.46 ± 2.50c 148.25 ± 2.25a 8.18 166.32 ± 3.43c 149.11 ± 4.00a 10.35 175.09 ± 3.22d 154.19 ± 4.17b 11.94
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Data represent the mean of three replicates analyzed separately ±standard deviation values and %D = percent of decrease; Values with different superscripts in rows are significantly (P ≤ 0.05) different.

The photosynthetic pigments are the most liable to be damaged by air pollution. Chlorophyll is said to be an index of productivity, hence any alteration in chlorophyll concentration may change the morphological, physiological, and biochemical behavior of the plant. From the analysis of the results of chlorophyll pigments, a considerable reduction was found at all the polluted sites compared to the control site during the entire study period. Results have shown the negative impact of brick kiln emissions on chlorophylls of the vegetable species namely Brassica oleracea, Phaseolus vulgaris L., and Solanum melongena L. At Site I (brick kiln site), a general decrease was observed in chlorophyll content as compared to Site II (Control site). This is probably due to the exchange of gaseous SO2 which causes direct injury to crops by entering the leaves through the stomata (Heather 2003) and dry or wet deposition of dust, fly ash, SO2, and NO2 on the leaves causing reduced interception of incident light and clogging of stomata (Chauhan and Joshi 2010). Investigations conducted elsewhere have shown that SOx, NOx, CO, and fly ash cause gross destruction of the thylakoid membrane system in the chloroplast (CLAG, 1996; Wellburn 1998; Liu et al. 2007). Injuries in the thylakoid are likely to be connected with a decline in the amount of chlorophyll (Malhotra and Hocking 1976). Pollutants can cause leaf injury, stomatal damage, premature senescence, and can decrease photosynthetic activity, disturb membrane permeability, and reduce growth and yield in sensitive plant species (Agrawal and Deepak 2003; Agrawal et al. 2006; Tiwari et al. 2006; Dwivedi and Tripathi 2007). The brick kiln emissions adversely affects the surrounding vegetation as the plants are exposed not to only one but too many air pollutants. Rao and Leblanc (1966) mentioned that high amount of gaseous SO2 causes destruction of chlorophyll and that might be due to the replacement of Mg+2 by two hydrogen atoms and degradation of chlorophyll molecules to phaeophytin. Mg++ is replaced by two molecules of hydrogen with a resulting change in the light absorption spectral properties of chlorophyll molecules.

A significant decrease in phaeophytin, carotenoids, proteins, carbohydrates, and lipid content was also noted in the samples collected at Site I (Brick kiln site) as compared to control site (S II). This could be attributed to brick kiln pollution stress as had confirmed by Ganai et al. (2010). Also phaeophytin and carotenoids content decreased on exposure to sulfur dioxide (Balkhi et al. 2009; Irshad et al. 2011). Carotenoids guard from photo‐oxidation damage; hence, their decrease has serious outcomes on chlorophyll pigments (Sifermann and Harms 1987). The decrease in protein concentration could be attributed to inactivation of enzymes due to air pollutants. At the higher concentration of pollutants like SO2 near brick kilns probably break enzymes and other proteins, enhanced the rate of protein denaturation, a fact being supported by the findings of Prasad and Inamdar (1990) and Constantinidou and Kozlowski (1979).

Carbohydrates are important constituent and source of energy for all living organisms. Plants manufacture this organic substance during photosynthesis and break down during respiration (Tripathi and Gautam 2007). In this study, carbohydrates in polluted leaves were reduced under pollution conditions. This could be fairly due to the destruction of photosynthetic pigments as a result of brick kiln emissions. These results are in consonance with the findings of Ganai et al. (2010). The concentration of carbohydrate is indicative of the physiological activity of a plant and it determines the sensitivity of plants to air pollution. Reduction in carbohydrate content at polluted site (Site I) can be attributed to increased respiration and decreased CO2 fixation because of chlorophyll deterioration (Tripathi and Gautam 2007). Davison and Barnes (1986) mentioned that pollutants like SO2, NO2, and H2S under hardening conditions can cause more depletion of carbohydrates in the leaves of plants grown in polluted area. The reaction of sulfite with aldehydes and ketones of carbohydrates can also cause reduction in carbohydrate content. The decrease in carbohydrate also could be due to the destruction of chlorophyll which adversely affects the rate of photosynthesis because of the competition between CO2 and SO2 for the carboxylase enzyme (Ziegler 1973).

Unlike other parameters’ lipids in samples collected at Site I (Brick kiln site) showed increasing trend with the increase in time duration, but lipid content was not increasing with such pace as in control samples. It is believed that lipids get accumulated when the growth is restricted during the autumn season (cold season) and were consumed during the growth period, that is, in summers (Meletiou‐Christou et al. 2011). Subsequently, when lipid content of Site I was compared to control samples (Site II), the reduction was seen in all the samples of vegetables. This is because of increasing pollution load in due course of time. According to detailed ultrastructural observations of plant cells injured by these air pollutants, cellular membrane systems are affected by the pollutants (Thomson 1975; Huttunen and Soikkeli 1984; Tiwari et al. 2006) and membrane permeability is also seen to change after treatment or exposure to SO2 and other pollutants (Malhotra and Hocking 1976; Mudd et al. 1984; Sakaki 2002).

Conclusions

Results have shown the negative impact of brick kiln emissions on biochemical parameters of the three vegetables Brassica oleracea, Phaseolus vulgaris L., and Solanum melongena L. Thus, the results of the current study provide evidence that brick kiln emissions are a significant risk to the vegetable plants in the Panzan area of district Budgam. As a result, it depicts that brick kilns are the prime reason for the deterioration of important consumable vegetables, which could lead to both food as well as health concern among the local population. Also, this will be a serious threat to millions of people depending on the vegetables grown near such kiln emission areas. The imbalance in the biochemical constituents in vegetables will lead to serious consequences on the overall living standard of exposed people in the near future if mushrooming of brick kilns is not controlled or replaced with new technology.

Conflict of Interest

None declared.

Acknowledgments

The authors are highly thankful to A. N. Kamili, Ex‐Head of Department of Environmental Science, University of Kashmir for providing necessary laboratory facilities as well as the transportation.

References

  1. Agbaire, P. O. , and Esiefarienrhe E.. 2009. Air pollution tolerance indices (APTI) of some plants around Otorogun gas plant in Delta State, Nigeria. JASEM 13:11–14. [Google Scholar]
  2. Agrawal, M. , and Deepak S. S.. 2003. Physiological and biochemical responses of two cultivars of wheat to elevated levels of CO2 and SO2, singly and in combination. Environ. Pollut. 121:189–197. [DOI] [PubMed] [Google Scholar]
  3. Agrawal, M. , Singh B., Agrawal S. B., Bell J. N. B., and Marshall F.. 2006. The effect of air pollution on yield and quality of mungbean grown in periurban areas of Varanasi. Water Air Soil Pollut. 169:239–254. [Google Scholar]
  4. Anda, A. 1986. Effect of cement kiln dust on the radiation balance and yields of plants. Environ. Pollut. 40:249–256. [Google Scholar]
  5. Ashenden, T. W. , and Williams I. A. D.. 1980. Growth reduction in Lolium multiflorum Lam. and Phleumpratense L. as a result of sulphur dioxide and nitrogen dioxide pollution. Environ. Pollut. 21:131–139. [Google Scholar]
  6. Ashger, M. S. , and Singh A. L.. 2003. Land degradation through brick kiln: A case study of Aligarh, India. Indian Journal of Regional Sciences. 35:77–84. [Google Scholar]
  7. Assadi, A. , Abdollah G. P., Fatemeh M., Nasrin T., and Leila A.. 2011. Impact of air pollution on physiological and morphological characteristics of Eucalyptus camaldulensis . J. Food Agric. Environ. 9:676–679. [Google Scholar]
  8. Balkhi, M. , Amin S., and Masood A.. 2009. Effect of aqueous sulphur dioxide on the biochemical and antioxidant properties of Malvasylvestris . Asian J. Environ. Sci. 3:139–145. [Google Scholar]
  9. Chauhan, A. , and Joshi P. C.. 2010. Effect of ambient air pollutants on wheat and mustard crops growing in the vicinity of urban and industrial areas. N. Y. Sci. J. 3:52–60. [Google Scholar]
  10. CLAG (Critical Loads Advisory Group) . 1996. Critical levels for air pollution for United Kingdom. Institute of Terrestrial Ecology, Penicuik. [Google Scholar]
  11. Constantinidou, H. A. , and Kozlowski T. T.. 1979. Effect of SO2 and O3 on Ulmusamericana seedling: visible injury, growth, carbohydrate, proteins and lipids. Can. J. Bot. 57:170–184. [Google Scholar]
  12. Davison, A. W. , and Barnes J. D.. 1986. Effects of winter stress on pollutant responses Pp. 16–32 in How are the effects of air pollutants on agricultural crops influenced by the interaction with other limiting factors? CEC, Brussels. [Google Scholar]
  13. Dubois, M. K. , Gilles J. K., Hamilton P. A.,Rebers, and F. Smith , 1951. A colorimetric method for the determination of sugar. Nature. 168:167. [DOI] [PubMed] [Google Scholar]
  14. Duxbury, A. C. , and Yentsch C. S.. 1956. Plankton pigment monographs. J. Mar. Res. 15:19–101. [Google Scholar]
  15. Dwivedi, A. K. , and Tripathi B. D.. 2007. Pollution tolerance and distribution pattern of plants in surrounding area of coal‐fired industries. J. Environ. Biol. 28:257–263. [PubMed] [Google Scholar]
  16. Emberson, L. D. , Ashmore M. R., Murray F., Kuylenstierna J. C. I., Percy K. E., Izuta T., et al. 2001. Impacts of air pollutants on vegetation in developing countries. Water Air Soil Pollut. 130:107–118. [Google Scholar]
  17. Ganai, B. A. , Aliya A., Masood A., Zargar M. A., and Ganaie S. A.. 2007a. Sulphite toxicity on spinach (Spinaceaoleracea). J. Res. Dev. 7:109–118. [Google Scholar]
  18. Ganai, B. A. , Nowsheen Q., Masood A., Zargar M. A., and Javaid I. B.. 2007b. Effect of sulphur dioxide on Malvasylvestris . J. Res. Dev. 7:19–24. [Google Scholar]
  19. Ganai, B. A. , Zaar A., Rafiq S. K., Masood A., Zargar M. A., and Kumar R.. 2010. Impact of brick kiln emissions on biochemical parameters of Malvasylvestris Lin. Ad. Plant Sci. 23:545–546. [Google Scholar]
  20. Godzik, S. , and Sienkiewicz J.. 1990. Air pollution and forest health in central Europe: Poland, Czechoslovakia, and the German Democratic Republic Pp. 155–170 in Grodzinski W., Cowling E. B. and Breymeyer A. I., eds. Ecological risks perspectives from Poland and the United States. National Academy Press, Washington, DC. [Google Scholar]
  21. Guttikunda, S. 2009. Impact analysis of brick kilns on the air quality in Dhaka. Sim‐Air Organization; Bangladesh: Retrieved from http://www.cgrer.uiowa.edu [Google Scholar]
  22. Heather, G. 2003. Effect of air pollution on agricultural crops. Ministry of Agriculture, ON, Canada. [Google Scholar]
  23. Huttunen, S. , and Soikkeli S.. 1984. Effects of various gaseous pollutants on plant cell ultrastructure Pp. 117–127 in Koziol M. J. and Whatley F. R., eds. Gaseous air pollutants and plant metabolism. Butterworths, London. [Google Scholar]
  24. Irshad, A. H. , Ahmad S. F., and Sultan P.. 2011. Effect of sulphur dioxide on the biochemical parameters of spinach (Spinaceaoleracea). Trakia J. Sci. 9:24–27. [Google Scholar]
  25. Knight, J. A. , Anderson S., and Rawle J. M.. 1972. Chemical basis of the sulfophosphovanillinreaction for estimating total serum lipids. Clin. Chem. 18:199–202. [PubMed] [Google Scholar]
  26. Kumar, S. R. , and Thambavani S. D.. 2012. Effect of cement dust deposition on physiological behaviors of some selected plant species. IJSTER 1:98–105. [Google Scholar]
  27. Lalitha, J. , Dhanam S., and Ganesh K. S.. 2013. Air pollution tolerance index of certain plants around SIPCOT industrial area Cuddalore, Tamilnadu, India. Int. J. Environ. Bioenergy 5:149–155. [Google Scholar]
  28. Likens, G. E. , Wright R. F., Galloway J. N., and Butler J.. 1979. Acid rain. Sci. Am. 241:43–51. [Google Scholar]
  29. Liu, N. , Peng C. L., Lin Z. F., Lin G. Z., and Pan X. P.. 2007. Effects of simulated SO2 pollution on subtropical forest succession: toward chlorophyll fluorescence concept. Pak. J. Bot. 39:1921–1935. [Google Scholar]
  30. Lowry, O. H. , Rosebrough N. J., Farr A. L., and Randall R. S.. 1951. Protein measurement with Folin reagent. J. Biol. Chem. 193:265. [PubMed] [Google Scholar]
  31. Maclean, D. C. 1981. Air Quality Standards for Fluoride to Protect Vegetation: Regional, Seasonal, and other Considerations. The 74th Annual Meeting and Exhibition of the Air Pollution Control Association, Philadelphia, PA.
  32. Malhotra, S. S. , and Hocking D.. 1976. Biochemical and cytological effects of sulphur dioxide on plant metabolism. New Phytol. 76:227–237. [Google Scholar]
  33. Mejstrik, V. 1980. The influence of low SO2 concentration on growth reduction of Nicotiana tabacum L. W. Samsum and Cucumis sativus L. C.V. Unikat. Environ. Pollut. 21:73–76. [Google Scholar]
  34. Meletiou‐Christou, M. S. , Banilas G. P., Bardis C., and Rhizopoulou S.. 2011. Plant biomonitoring: impact of urban environment on seasonal dynamics of storage substances and chlorophylls of Oleander . Global NEST 13:395–404. [Google Scholar]
  35. Miller, P. R. 1983. Ozone effects in the San Bernardino National Forest Pp 161–197 in Proceedings of symposium on air pollution and the productivity of the forest. Pennsylvania State University Press, State College, Pennsylvania. [Google Scholar]
  36. Mudd, J. B. , Banerjee S. K., Dooley M. M., and Knight K. L.. 1984. Pollutants and plant cells: effects on membranes Pp. 105–116 in Koziol M. J. and Whatley F. R., eds. Gaseous air pollutants and plant metabolism. Butterworths, London, U.K. [Google Scholar]
  37. NAPAP (National Acid Precipitation Assessment Program) . 1990. Effects of pollution on vegetation. Government Printing Office, Washington, DC. [Google Scholar]
  38. Nihlgard, B. 1985. The ammonium hypothesis ‐ an additional explanation to the forest dieback in Europe. Ambio. 14:844. [Google Scholar]
  39. Pawar, K. , and Dubey P. S.. 1983. Effect of atmospheric pollutant on the morphology and pigment content in proceeding of sixth world congress on air quality. Paris 2:501–507. [Google Scholar]
  40. Pawar, K. , Dube B., Maheshwari R., and Bafna A.. 2010. Biochemical aspects of air pollution induced injury symptoms of some common ornamental road side plants. Int. J. Biol Med. Res. 1:291–294. [Google Scholar]
  41. Prasad, M. S. V. , and Inamdar J. A.. 1990. Effect of cement kiln dust pollution on black gram (Vignamungo). Proc. Indian Acad. Sci. (Plant Sci.) 100:435–443. [Google Scholar]
  42. Rajput, M. , and Agrawal M.. 2004. Physiological and yield responses of pea plants to ambient air pollution. Indian J. Plant Physiol. 9:9–14. [Google Scholar]
  43. Rao, D. N. 1981. Phytomonitoring of air pollution. Osmania University, Hyderabad, WHO workshop on biological indicator and indices of Environmental Pollution: Pp. 1–8. [Google Scholar]
  44. Rao, M. V. , and Dubey P. S.. 1988. Plant response against SO2 in field conditions. Asian Environ. 10:1–9. [Google Scholar]
  45. Rao, D. N. , and Leblanc F.. 1966. Effects of SO2 on the lichen algae with special reference to chlorophyll. Biologist 69:69–95. [Google Scholar]
  46. Sakaki, T. 2002. Effects of air pollutants on lipid metabolism in plants. Air Pollut. Plant Biotechnol 1:93–109. [Google Scholar]
  47. Shannigrahi, A. S. , Fukushima T., and Sharma R. C.. 2004. Anticipated air pollution tolerance of some plant species considered for green belt development in and around an industrial/urban area in India: an overview. Int. J. Environ. Stud. 61:125–137. [Google Scholar]
  48. Sifermann‐Harms, D. 1987. The light harvesting and protective functions of carotenoids in photosynthetic membranes. Physiol. Plant 69:561–568. [Google Scholar]
  49. Singh, L. B. 1990. Phytotoxic influence of SO2 pollution on leaf growth of Vigina mungo L. J. Environ. Biol. 11:111–120. [Google Scholar]
  50. Skinder, B. M. , Pandit A. K., Sheikh A. Q., and Ganai B. A.. 2014. Brick kilns: cause of atmospheric pollution. J. Pollut. Eff. Cont. 2:110. [Google Scholar]
  51. Sokal, R. R. , and Rohlf F. J.. 1981. Biometry: the principles and practice of statistics Pp. 859 in Freeman and Company, San Francisco W. H., ed. Biological research, 2nd ed W. H. Freeman and Co, New York, NY. [Google Scholar]
  52. Strain, H. N. , Bengavin T. C., and Walter A. S.. 1971. Analytical procedure for isolation, identification, estimation and investigation of chlorophyll Pp. 452–476 in Pietro A. S., ed. Methods in enzymology. Academic Press, New York, NY. [Google Scholar]
  53. Su, Y. C. , Ho C. L., Wang E. I., and Chang S. T.. 2006. Antifungal activities and chemical compositions of essential oils from leaves of four eucalyptus . Taiwan Journal of Forest Science. 21:49–61. [Google Scholar]
  54. Thomas, H. 1991. Accumulation and consumption of solutes in swards of Lolium perenne during drought and after rewatering. New Phytol. 118:35–48. [Google Scholar]
  55. Thomson, W. W. 1975. Effects of air pollutants on plant ultrastructure Pp. 179–194 in Mudd J. B. and Kozlowski T. T., eds. Responses of plants to air pollution. Academic Press, New York, NY. [Google Scholar]
  56. Tiwari, S. , Agrawal M., and Marshall F. M.. 2006. Evaluation of ambient air pollution impact on carrot plants at a sub urban site using open top chambers. Environ. Monit. Assess. 119:15–30. [DOI] [PubMed] [Google Scholar]
  57. Tripathi, A. K. , and Gautam M.. 2007. Biochemical parameters of plants as an indicator of air pollution. J. Environ. Biol. 28:127–132. [PubMed] [Google Scholar]
  58. Unsworth, M. H. , and Harrison R. M.. 1985. Is lead killing German forests? Nature 317:674. [Google Scholar]
  59. Vernon, L. P. 1960. Spectrophotometric determination of cholorophyll and phaeophytin in plant extracts. Anal. Chem. 32:1144–1150. [Google Scholar]
  60. Warren, J. L. 1973. Green space for air pollution control: school of forest resources. Technical Report No. 50, North Carolina State University, Raleigh, NC. [Google Scholar]
  61. Wellburn, A. 1998. Sulfur dioxide Pp. 23–59 in Air pollution and acid rain: the biological impact. Longman Scientific and Technical, John Wiley & Sons, New York. [Google Scholar]
  62. Ziegler, E. 1973. Effects of sulfite on PEP‐carboxylase and malate formation in extracts of Zea mays . Photochemistry 12:1027–1030. [Google Scholar]

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