The accumulation and distribution of pp′DDT and related compounds in an apple orchard .I. residues in the soil

Soils from an orchard sprayed annually (1953-1969) with technical DDT (77% pp′DDT and 22 % pp′DDT) were analysed for residues from 1964 until 1969. The amount of DDT found after 17 years was 21 %pp′DDTout of 27.1 kg/ha applied, and 7 % of pp′DDT out of 7.6 kg/ha. The vertical distribution of residues (pp′DDT, pp′DDE, pp′TDE and pp′DDT) showed a linear relationship between log amount and depth, with approximately 80% in the top 10 cm of soil. At depths from 50 to 210 cm, residue values were too small to be determined (i.e. < 1 ng/g dry wt). The surface distribution in the orchard showed a systematic pattern of circular areas of residues, with maximum values centred at each trunk (7.5 μg/g) and decreasing rapidly to each alley (1.9 ug/g). The levels of pp′DDT had reached a steady state (3-4 kg/ha) and the half-life time was calculated as 3.0 j′ears. pp′DDE (1.8 kg/ha) was the main metabolite of pp′DDT. Small amounts of pp′TDE were also found, pp′DDT was less persistent than pp′DDT, with a half-life time of 1.5 years.     

Distribution and breakdown of DDT in orchard soil

Amounts of DDT and its breakdown products were determined in soil in an apple orchard in Herefordshire. Samples were taken for a number of years (1972–79) after use of the insecticide in the orchard had ceased in 1969. The results were compared with those obtained in an investigation of the same orchard in 1968. From 1968 to 1979, soil residues of pp′-DDT, p′--DDT and pp′--TDE decreased gradually whereas those of pp′--DDE increased, and there were linear relationships between log (concentration) and time. The calculated time for 50% decrease in concentration (Dt₅₀) was 11.7 years for pp′--DDT, 3.3 years for pp′--TDE and 7.1 years for op′--DDT; the time for doubling the concentration for pp′--DDE was 9.1 years. Regression analysis on the two major components (pp′--DDT+pp′--DDE) indicated that the total amount (2.7 mg kg^?1) was not decreasing with time. It was concluded that during a post-spray era, the breakdown of pp′--DDT to pp′--DDE was a significant feature of the persistence of DDT, and that, in contrast to the findings of other workers who sampled when DDT was being used, there were no losses by volatilisation. There was an exponential decrease in the amount of DDT residues with increasing soil depth and approximately 90% was found in the top 10 cm of the undisturbed soil profile.     

Studies on the mechanism of estrogenic actions of o,p′DDT: Interactions with the estrogen receptor

The ability of o,p′DDT to bind to the 8S moiety in the uterine cytosol or to interfere with the binding of ³H-estradiol-17β (³H-E₂) to that binding component was investigated utilizing a 10–30% sucrose gradient sedimentation analysis. Attempts to demonstrate the binding of radiolabeled o,p′DDT to the 8S receptor in the mouse and rabbit were not successful, presumably due to the relatively low specific activity of the radiolabeled o,p′DDT, however, binding to the “nonspecific” 4S site(s) was detected. On the other hand, the addition of nonlabeled o,p′DDT inhibited the binding of ³H-E₂ to the 8S receptor. Thus, o,p′DDT (2 μM) suppressed by 58% the binding of ³H-E₂ (2 nM) in the 8S region in ovariectomized adult mice. Similarly, in immature rats three concentrations of o,p′DDT (16, 32, and 96 μM) inhibited by 39.5, 52.9, and 59.7% respectively, the binding of ³H-E₂ (2.8 nM). Similar results were obtained with uterine preparations from mature rats. However, the suppression of binding of ³H-E₂ in the 8S region resulted in an increased binding in the 3–4S region.A Scatchard plot analysis of the binding of ³H-E₂ in the presence of o,p′DDT revealed the same number of binding sites as in the absence of o,p′DDT, indicating that o,p′DDT did not “destroy” the binding capacity. Also, this analysis revealed that o,p′DDT merely caused a decrease in the ratio of the bound to free E₂, indicating that o,p′DDT binds to the receptor and thus interferes with E₂ binding.In addition, our observations that the administration of o,p′DDT to immature female rats causes a marked increase in the levels of the uterine nuclear binding sites (nuclear estogren receptor) is a further indication that o,p′DDT acts as a typical estrogenic compound. However, whether o,p′DDT has antiestrogenic activity as well has not been established.     

Expression and inheritance of nerve insensitivity resistance in larvae of Helicoverpa armigera (Lepidoptera: Noctuidae) from China

Nerve insensitivity resistance to synthetic pyrethroids was detected in a resistant field strain (JSFX-R) of the cotton bollworm, Helicoverpa armigera (Hübner), using a neurophysiological assay in which extracellular spontaneous neuronal activity was measured in response to cis-cypermethrin. The nerve insensitivity mechanism was selected using a combination of toxicological and neurophysiological methods. The third-instar larvae in selected strains of Family-37 and CTR strain expressed a very high resistance to fenvalerate (RF = 2060-fold and 805-fold, respectively) and high cross-resistance to DDT (RF = 1927-fold and 2384-fold, respectively) which was not affected by two metabolic synergists, PBO and DMC. The frequency of nerve-insensitive individuals detected in neurophysiological assays (54, 81 and 100% for JSFX-R strain, and the selected strains Family-43 and Family-37, respectively) was not only positively correlated (R² = 0.968) with the frequency of non-PBO-synergisable resistant individuals detected in toxicological tests (37.5, 62.5 and 90% for JSFX-R strain, Family-43 and Family-37, respectively), but also positively correlated (R² = 0.978) with the frequency of DDT-resistant individuals detected in toxicological tests (40, 67.5 and 93.3% for JSFX-R strain, Family-43 and Family-37, respectively). Analysis of dose–mortality lines to DDT and fenvalerate from F₁ hybrids (R♀ × S♂) indicated that nerve insensitivity resistance to DDT and fenvalerate in the CTR strain was inherited in an incompletely recessive pattern. Degree of dominance (D) was estimated to be −0.66 (± 0.06) (DDT) and −0.26 (± 0.04) (fenvalerate). The dose–mortality curves to DDT in back-cross progeny were strongly suggested, by chi-square analysis, to be fitted with those expected of a one-gene model. Evidence for the co-existence of nerve insensitivity and oxidative metabolic resistance mechanisms within individual H armigera and the effects of their interaction on the expression of resistance to fenvalerate are discussed. © 1999 Society of Chemical Industry     

Accumulation and distribution of pp′-DDT and related compounds in an apple orchard. II. Residues in trees and herbage

DDT residues in or on the roots and leaves of the herbage and the roots, bark, leaves and fruit of the trees are given for an apple orchard sprayed annually (1953–1969). The distribution of DDT in both the grass and the grass roots was in circular areas of residues, with maximum values at each trunk and decreasing radially to each alley. Of the spray applied at the green cluster stage 80% was deposited on the grass sward and very little, if any, directly on the soil surface. The pp′-DDT content of the grass fell rapidly with successive mowings (from which the cuttings remained in situ) from 400 μg/g at spraying to 2 μg/g after nine months. 33 g/ha pp′-DDT was found in the herbage roots (0.87% of the total residues in the soil). The residues in the bark (87.5 g/ha) were much lower than expected after 13 years spray application. There were increased amounts of pp′-DDE, pp′-TDE and pp′-TDEE relative to pp′-DDT, indicating some breakdown on the bark, but the chief losses were attributed to volatilisation and to removal by wind and rain. The residue content of root bark varied from 3 μg/g near the emerging trunk to 0.05 μg/g at a depth of 90 cm. The pp′-DDT content of leaves at leaf fall rose from <1 ng/g after a single spring spray to 8.33 μg/g following an additional spray in late June. There was a large loss of DDT from the canopy between the June spray and leaf fall (440–480 g/ha down to 25 g/ha), attributed to volatilisation. The amount of pp′-DDT on the fruit, after a single spray, was 3 ng/g fresh weight (80.9 mg/ha out of a total of 1.0–1.5 kg/ha used).     

气相色谱-串联质谱法测定莲雾中的灭蚁灵和哒螨灵残留

建立了同时测定莲雾Syzygium samarangense(Bl.)Merr.et Perry中灭蚁灵和哒螨灵残留的气相色谱-串联质谱(GC-MS/MS)分析方法。样品经乙腈匀浆提取,石墨化碳黑/氨基混合型固相萃取柱净化,GC-MS/MS检测。采用所建立的方法,在0.01~0.5 mg/kg下进行添加回收试验,2种农药的平均回收率在89%~102%之间,相对标准差为1.7%~5.2%(n=5);方法的线性范围为0.01~0.5 mg/L,决定系数(R2)0.99;对灭蚁灵和哒螨灵的定量限均为0.005 mg/kg。所建方法能满足莲雾中灭蚁灵和哒螨灵残留同时检测的要求。     

高效液相色谱法测定稻田样品中3种新烟碱类杀虫剂残留

采用带紫外检测器的高效液相色谱仪(HPLC-UV),建立了同时检测呋虫胺、吡虫啉和啶虫脒在稻田水、稻田土壤、水稻植株、稻秆、稻壳和糙米中残留量的检测方法。稻田水、稻田土壤、水稻植株、稻秆、稻壳样品用乙腈提取,糙米样品用V(乙腈)∶V(水)=1∶1混合溶液提取。稻田水无需净化,其余样品用弗罗里硅土柱净化。HPLC-UV测定,流动相为V(甲醇)∶V(水)=30∶70,流速采用梯度流速,紫外检测波长为254 nm。结果表明:在0.05~10 mg/L范围内,3种农药的质量浓度与其相对应的色谱峰面积之间呈良好的线性关系,线性方程分别为呋虫胺:y=62.55x+4.039 2(R2=0.999 2);吡虫啉:y=99.968x+7.525 1(R2=0.998 6);啶虫脒:y=97.084x+6.072(R2=0.999 4)。在0.05~2 mg/kg添加水平下,样品中呋虫胺、吡虫啉和啶虫脒的平均回收率在81%~99%之间,相对标准偏差(RSD,n=5)在1.2%~7.9%之间。该方法的前处理过程较简单,且准确度、精密度和灵敏度均符合农药残留分析的技术要求。     

固相萃取-气相色谱-串联质谱法测定大蒜中19种有机磷农药残留量

建立了采用固相萃取(SPE)结合气相色谱-三重四级杆串联质谱(GC-MS/MS)测定大蒜中19种有机磷农药残留量的方法。采用V(乙酸)∶V(乙酸乙酯)=1∶99混合溶液提取,Carbon/NH2固相萃取小柱净化,在GC-MS/MS的多反应(MRM)模式下进行外标法定量。结果表明:在0.04~0.8 mg/L范围内,19种农药的色谱峰面积与其相应的质量浓度间均呈良好的线性关系;所有供试农药检测方法的定量限(LOQ)均低于0.01 mg/kg;在0.01~0.2 mg/kg添加水平下,19种农药的平均回收率在68.0%~130%之间,相对标准偏差(RSD)≤15.6%。该方法背景干扰少,灵敏度高,适合基质复杂的大蒜样品中有机磷农药残留量的检测。     

气相色谱-串联质谱法检测乙氧氟草醚、唑草酮和乙螨唑在4种香辛料中的残留

建立了气相色谱-三重四极杆串联质谱 (GC-MS/MS)检测留兰香、桂皮、薄荷和月桂叶中乙氧氟草醚、唑草酮、乙螨唑残留的分析方法。4种香辛料用超纯水饱和,乙腈提取,无水硫酸镁及氯化钠盐析,氨基/石墨化碳黑 (NH₂-Carb) 固相萃取柱净化,多反应监测模式,气相色谱-串联质谱测定。结果表明:乙氧氟草醚在0.002 5~2 mg/L范围内,唑草酮和乙螨唑在0.01~2 mg/L范围内,3种农药的进样质量浓度与对应的峰面积间呈良好的线性关系,r > 0.99;乙氧氟草醚在0.025、0.5和2 mg/kg 3个添加水平下,在4种香辛料中的平均回收率在86%~112%之间,相对标准偏差 (RSD)在2.4%~9.6%之间;唑草酮在0.2、0.5和2 mg/kg 3个添加水平下的平均回收率在87%~114%之间,RSD在2.4%~11%之间;乙螨唑在0.5、2和5 mg/kg 3个添加水平下的平均回收率在86%~116%之间,RSD在3.2%~11%之间。乙氧氟草醚、唑草酮和乙螨唑在4种香辛料中的定量限 (LOQ) 分别为0.025、0.2和0.5 mg/kg。     

Mechanisms of DDT resistance in larvae of the mosquito Aedes aegypti L

Larvae of eight strains of Aedes aegypti were exposed to DDT and compared for resistance, DDT uptake, in-vivo breakdown of DDT and residual unmetabolised DDT. Resistance varied widely between strains, three being fully susceptible, two almost immune and three of intermediate resistance. Breakdown of DDT by dehydrochlorination to 1,1-dichloro-2,2-bis(4-chlorophenyl)ethylene (pp'-DDE) occurred in all strains and was greater in the five resistant types, but there was no significant correlation between the extent of breakdown in the resistant strains and the level of resistance. Moreover the overall difference between susceptible and resistant strains disappeared when they were compared at a low, almost sublethal, concentration of DDT. Larvae of resistant strains carried a greater absolute quantity of unmetabolised DDT in the body and were able to tolerate levels of DDT that were lethal to susceptible larvae. However the two most resistant strains (T8 and B51) contained significantly less DDT plus pp'-DDE than strains of intermediate resistance (T30 and BSJ) from which they had been derived. Addition of the synergist chlorfenethol to DDT increased its knockdown effect on all resistant strains, suggesting that dehydrochlorination was a factor in resistance. Three strains, two DDT-resistant and one DDT-susceptible, were tested with 1,1-bis(4-ethoxyphenyl)-2,2-dimethylpropane (I), an insecticide that cannot be dehydrochlorinated. All the strains were relatively tolerant to it although the DDT-susceptible strains were less tolerant. Addition of the synergist sesamex decreased the level of tolerance to I in all strains which suggested that microsomal oxidation made some contribution to it. It is concluded that three factors contribute to larval DDT resistance in A. aegypti; (a) increased metabolism to pp'-DDE; (b) increased tolerance to unmetabolised internal DDT; and (c) reduced content of DDT+pp'-DDE (only in the most resistant strains and due either to reduced absorption or increased excretion). These factors are discussed in relation to known larval resistance genes R^DDT1 and y.     

Organochlorine pesticides and polycyclic aromatic hydrocarbons in water and sediment of the Bosten Lake,Northwest China

We evaluated organic pollution in Bosten Lake, Xinjiang, China, by measuring the concentrations and distributions of organochlorine pesticides(OCPs) and polycyclic aromatic hydrocarbons(PAHs). Water and sediment samples were collected from 19 sites(B1–B19) in the lake for analysis. Our analytical results show that the concentrations of total OCPs in water ranges from 30.3 to 91.6 ng/L and the concentrations of PAHs ranges from undetectable(ND) to 368.7 ng/L. The concentrations of total OCPs in surface(i.e., lake bottom) sediment ranges from 6.9 to 16.7 ng/g and the concentrations of PAHs ranges from 25.2 to 491.0 ng/g. Hexachlorocyclohexanes(HCHs) and dichlorodiphenyltrichloroethanes(DDTs) account for large proportions of the OCPs. Low α- to γ-HCH ratios in both water and sediment samples indicate possible contributions from both industrial products and lindane. DDTs in water are probably from historical input, whereas DDTs in sediments are from both historical and recent inputs. Moreover, DDT products in both water and sediments were from multiple sources in the northwestern part of the lake(B11, B12, B13, and B14). Fugacity ratios for DDT isomers(p,p′-DDE and p,p′-DDT) at these sites were generally higher than equilibrium values. These results suggest that the input from the Kaidu River and diffusion of DDTs from the sediment to the water are responsible for DDT pollution in the water. Lower-molecular-weight PAHs, which originate primarily from wood and coal combustion and petroleum sources, represent the major fraction of the PAHs in both water and sediment samples. Our findings indicate that OCPs and PAHs in Bosten Lake can be attributed primarily to human activities. A risk assessment of OCPs and PAHs in water and sediment from Bosten Lake, however, suggests that concentrations are not yet high enough to cause adverse biological effects on the aquatic ecosystem.     

Cross-resistance spectrum in pyrethroid-resistant Culex quinquefasciatus

Strains of Culex quinquefasciatus Say, selected with biopermethrin [(1R)-trans-permethrin] or with (1R)-cis-permethrin, were examined in the larval stage for crossresistance to 30 pyrethroids, DDT, dieldrin, temephos, propoxur, and two organotin compounds. The (1R)-trans-Permethrin-R strain [resistance factor (RF) = 4100-fold] and the (1R)-cis-Permethrin-R strain (RF= 450-fold) of C. quinquefasciutus were cross-resistant to all pyrethroids tested [RF= 12-fold for an allethrin isomer to about 6000-fold for (RS,RS)-fenvalerate] as well as to DDT (RF= about 2000-fold). However, they were not significantly Cross-resistant to dieldrin, temephos, propoxur, and the two organotin compounds. Changes in the alcohol moiety, structural isomerism, and susceptibility of the cyclopropane C-3 side chain to oxidative attack are important factors in determining the level of cross-resistance to various pyrethroids. Limited synergism of the pyrethroids by S,S,S-tributyl phosphorotrithioate and piperonyl butoxide (PB), and of DDT by chlorfenethol and PB, suggested that some non-metabolic mechanism, such as kdr, may be an important component of resistance to pyrethroids as well as to DDT in this mosquito.     

气相色谱法测定元胡、浙贝母和白芍中嘧霉胺残留

建立了一种测定元胡、浙贝母和白芍3种中药材中嘧霉胺残留的气相色谱分析方法。样品经二氯甲烷提取,液-液分配,柱层析[m（中性氧化铝）:m（弗罗里硅土）=3:2]净化,气相色谱-氮磷检测器（GC-NPD）检测,基质匹配外标法定量,同时经气相色谱-串联质谱（GC-MS/MS）验证。结果表明:在0.02~10 mg/L范围内,分别以正己烷和3种空白基质溶液为溶剂配制嘧霉胺的标准工作溶液,峰面积与相应的质量浓度间呈良好的线性关系,R2均大于0.999;在0.01（元胡中为0.02）、0.1和0.5 mg/kg 3个添加水平下,添加回收率为75%~104%,日内相对标准偏差（RSD）为1.3%~10.2%（n=5）,日间RSD为1.2%~9.0%（n=3）。分析方法在元胡、浙贝母和白芍中的定量限（LOQ）分别为0.02、0.01和0.01 mg/kg。该方法的灵敏度、准确度及精密度均符合农药残留分析要求,且简单易行,净化效果好,适用于元胡、浙贝母和白芍中嘧霉胺分析。     

The metabolism of p,p′-DDT by the feral pigeon (Columba livia)

Male feral pigeons were dosed with ring-labeled $\text{[}{}^{14}\text{C}\text{]p,p′-}\text{DDT}$ and the tissues and droppings analyzed for total ¹⁴C, extractable ¹⁴C, and metabolites. Only 16% of an intraperitoneal dose of 1.5–2.2 mg kg^?1 was voided in the droppings over 28 days; the rate of loss reached a maximum on the 14th day and then fell quickly away. The rate of removal of ¹⁴C in droppings was low in comparison to that found in the rat and the Japanese quail. When pigeons were dosed with 32–38 mg kg^?1 DDT per bird, and killed after 77 days, 5.4% of the dose was eliminated in droppings and 87% was recovered in the body. The tissues and droppings from this experiment were analyzed for DDT and its metabolites. Of the ¹⁴C remaining in tissues 88% was accounted for as the apolar compounds DDE, DDT, and DDD. Approximately half of the ¹⁴C in droppings was present as DDE, DDT, and DDD, whereas 27–35% was apparently in conjugated form, extractable from aqueous solutions by ethyl acetate after prolonged acid hydrolysis. Two polar metabolites were isolated from the acid-released material. One was p,p′-DDA; the other was extractable from aqueous solution at pH 8 and was tentatively identified as a monohydroxy derivative of p,p′-DDT. DDE accounted for 93% of the ¹⁴C present as metabolites in tissues and droppings, clearly indicating the importance of this intermediate in this study. The metabolism of DDT in the feral pigeon is discussed in relation to its metabolism by other species.     

Inhibition of acetyl-coenzyme a carboxylase by coenzyme a conjugates of grass-selective herbicides

A total of 146 samples of different kinds of cheeses produced in Spain were analysed in order to ascertain the specific contamination pattern. The organochlorine compounds studied were those most commonly investigated in previous surveys: α-HCH, β-HCH, γ-HCH (lindane), γ-HCH, chlordane, aldrin, dieldrin, endrin, heptachlor, heptachlor epoxide, and the isomers and metabolites of DDT. α-HCH, β-HCH, γ-HCH, chlordane, p,p′, DDT, and p,p′-DDE were found in more than 76% of samples; p,p′-DDE and γ-HCH were the most frequently detected, with frequencies of 100 and 97.9% respectively. γ-HCH, aldrin, dieldrin, heptachlor, heptachlor epoxide, o,p′-DDT, p,p′-DDD and o,p′-DDD were observed at lower frequencies. No residues of endrin were detected in any sample. Insecticides exceeding the maximum residue limits (MRLs) were chlordane, β-HCH, α-HCH and γ-HCH, with 42, 20, eight and six samples respectively. Mean residues of organochlorines found were as follows (μ kg^?1 butterfat): α-HCH = 46.3; β-HCH = 46.5; γ-HCH = 54.2; δ-HCH = 16.9; aldrin = 16.7; dieldrin = 9.7; heptachlor = 15.9; heptachlor epoxide = 14.8; chlordane = 50.2; o,p′-DDT = 5.1; p,p′-DDT = 12.4; o,p′-DDT = 19.6; p,p′-DDD = 46.7; o,p′-DDE = 6.9; p,p′-DDE = 40.7 (.DDT = 55.0). Estimated dietary intakes (EDIs) from cheese consumption were compared to acceptable daily intakes (ADIs) for the pesticides where residues exceeded the MRL. EDIs calculated were in all cases below ADIs, and, therefore, based on the ADIs, there is no health risk involved in the consumption of cheese from Spain arising from organochlorine residues.     

Action of deltamethrin on the calcium/calmodulin-dependent protein kinase from the rat brain

The action of deltamethrin on the calcium/calmodulin-dependent protein kinase (CaM-Kinase II) and phosphatase system in the rat brain synapse was studied under various experimental conditions to optimize these enzyme activities and to facilitate the studies of the mechanism of interaction of this pesticide with several components of this enzyme system. To obtain a clear-cut inhibition of this enzyme by deltamethrin the following conditions must be met: (a) the enzyme system should be purified by precipitation with ammonium sulfate (450 g litre^?1) prior to the addition of deltamethrin, (b) both Ca²⁺ and calmodulin (CaM) should be added to the incubated media before the addition of [y-³²P]ATP, (c) deltamethrin should be incubated at least 10 min (but less than 30 min) with the enzyme system before [y-³²P]ATP addition, (d) the incubation temperature should be above 20°C (optimum 30°C), (e) [y-³²P]ATP concentration should be in the order of 10^? M (concentration adjusted using cold ATP), and (f) the incubation time with [y^?P]ATP for incorporation of ³²P into the protein should be in the neighborhood of 60 s. Under these conditions, the inhibitory potency of various active and inactive isomers or analogs of pyrethroids and DDT was tested. The order of the inhibitory power of these active forms of pesticides was 1 R-deltamethrin > (S)(RS) fenvalerate ≥ p,p′-DDT. Other compounds were not active at the concentration tested, indicating the differential sensitivity of this enzyme and the existence of a correlation of inhibitory power to insecticidal activity.     

Inactivation of Paraquat by an Aqueous Extract of Rehmannia glutinosa

Rehmannia glutinosa (Gaertn.) Libosch. ex Fisch. & Mey. was very tolerant to paraquat (1,1′-dimethyl-4,4′-bipyridinium). The paraquat concentration required to reduce dry weight of R. glutinosa by 50% (GR₅₀) was 24 mM , whereas a similar effect was obtained with 0·75 mM in Zea mays L. (maize, cv. Dekalb) and Glycine max (L.) Merr. (soybean, cv. Kwangkyo). When 1·5 mM paraquat in 10% aqueous extract of R. glutinosa was applied to maize and soybean, growth inhibition reached 24% and 7%, respectively, of the untreated control. Decreased activity of paraquat due to the extract also occurred in both leaf discs and chloroplasts of soybean. The total amount of [¹⁴C]paraquat absorbed into soybean leaves after 48 h was 34%, but it was reduced to 17% when the extract was added. Translocation of [¹⁴C]paraquat was also inhibited in the presence of the extract. In thin-layer chromatography (TLC) analysis using various solvent systems, R_f values of [¹⁴C]paraquat with the extract differed from those without the extract. The results suggested that the aqueous extract of R. glutinosa contained a substance which could nullify paraquat activity. © 1997 SCI.     

气相色谱-串联质谱法测定植物样品中17种有机氯农药和8种多氯联苯

建立了植物样品中17种有机氯农药和8种多氯联苯单体的气相色谱-串联质谱(GC-MS/MS)分析方法。样品以 V(丙酮):V(乙酸乙酯)=1:1为溶剂进行提取,采用石墨化炭黑及氨基联合SPE小柱净化,GC-MS/MS测定。25种化合物的平均添加回收率在66.6%~113.1%之间,相对标准偏差(RSD)在4.1%~14.1%之间,方法检出限(MDL)在0.03~0.29 ng/g之间。该方法灵敏度高,满足环境调查的需求。对污染区采集的植物样品进行检测,发现被变压器油污染地区的植物体内含有较高质量分数的PCB28和PCB52,最高达108 ng/g,说明多氯联苯能够通过迁移等途径从土壤传递到植物中。     

Comparative excretion of DDT analogues into milk of indian buffalo,Bubalus bubalis L. following oral administration

Four groups of Indian buffaloes were fed daily with 25 mg of p,p′-DDT p,p′-TDE p,p′-DDE or o,p′-DDT for 100 days. Milk was analysed for organochlorine residues during this period and also for 100 days after pesticide administration had been discontinued. For the period showing ‘plateau level’ residues, 17.2% of p,p′-DDE, 17% of p,p′-TDE, 14% of p,p′-DDT as p,p′-DDT (3.5%); p,p′-TDE (10.5%); 3.2% of p,p′-DDT as o,p′-DDT (1.3%) and o,p'-TDE (1.9%) of their administered amounts were excreted in the milk. Since these compounds were excreted at different rates, the residue levels in the milk expected from a given feed would depend on their concentration and proportional distribution in the feed. The maximum tolerable content of DDT analogues in feed was derived to be 0.1 mg kg^?1 (dry weight basis) by using the maximum accumulation coefficient and incorporation of the necessary safety margin. It is concluded that Indian buffaloes fed with rations contaminated with a total of DDT analogues below this limit will yield milk of acceptable quality. Following the termination of feeding with contaminated rations, the elimination of p,p′-DDE in the milk took the longest time and that of o,p′-DDT the shortest. These results suggest that the time required for the initial high residue concentration to decline to less than the legal limit would be determined by the relative amounts of DDE, TDE and DDT in the milk, after elimination of the potent source of contamination.     

Behaviour of ddt in three soils exposed to solar radiations under different conditions

Volatilization, mineralization, degradation and binding of soil-applied [¹⁴C]DDT were studied in three different soils from a tropical region of southern India subjected to solar irradiation and flooding for a period of 42 days. The soil types–red cotton soil, nursery soil and canal bank soil–differed in their organic carbon content, pH and texture. Under unflooded conditions, volatile losses were highest in the sandy canal bank soil. Flooding significantly enhanced volatilization, and this effect was maximal in the nursery soil, which had the highest organic carbon. The soils fully exposed to solar radiations in quartz tubes registered 1.5-1.8 times greater volatility. The volatilized organics contained appreciable quantities of DDE under both flooded and unflooded conditions. In addition, greater quantities of DDD volatilized from the flooded systems. The rate of formation of DDE was faster when soils were irradiated in quartz tubes. Mineralization remained minimal throughout the period of exposure and flooding the soil appeared to reduce further the [¹⁴C]carbon dioxide evolution. Canal bank soil exhibited the least mineralization and degradation. The data indicate that volatilization was significantly influenced by solar radiation and flooding to a much greater degree than by the differences in soil properties. Binding of DDT to soil was significantly increased by flooding the soil, thus leaving up to 33% of the initial DDT as bound residues in the nursery soil.