Microbial metabolism of quinoline and related compounds. II. Degradation of quinoline by Pseudomonas fluorescens 3, Pseudomonas putida 86 and Rhodococcus spec. B1

Quinoline catabolism was investigated with different bacterial strains, able to use quinoline as sole source of carbon, nitrogen and energy. Some degradation products of quinoline were isolated from the culture fluids and identified. With Pseudomonas fluorescens and Pseudomonas putida we found 2-oxo-1,2-dihydroquinoline, 8-hydroxy-2-oxo-1,2-dihydroquinoline, 8-hydroxycoumarin and 2,3-dihydroxyphenylpropionic acid as intermediates. With a Rhodococcus strain 2-oxo-1,2-dihydroquinoline, 6-hydroxy-2-oxo-1,2-dihydroquinoline, a red meta-cleavage product and a blue fluorescent compound were isolated. The red compound was identified as 5-hydroxy-6-(3-carboxy-3-oxopropenyl)-1H-2-pyridone. From this the blue fluorescent azacoumarin 2H-pyrano-2-one-[3,2b]-5H-6-pyridone is formed by chemical decomposition. Therefore it can be considered a by-product of quinoline-degradation in Rhodococcus spec. With the present results two different degradation pathways for quinoline in different microorganisms are proposed.     

Microbial Metabolism of Quinoline by Comamonas sp.

An aerobic bacterial strain which can use quinoline as the sole carbon and energy source has been isolated from activated sludge and identified as Comamonas sp. The microbial metabolism of quinoline by this strain has been investigated. A pH 8 and a temperature of 30 °C were the optimum degradation conditions of quinoline. Five intermediates including 2-oxo-1,2-dihydroquinoline, 5-hydroxy-6-(2-carboxyethenyl)-1H-2-pyridone, 6-hydroxy-2-oxo-1,2-dihydroquinoline, 5,6-dihydroxy-2-oxo-1,2-dihydroquinoline, and 8-hydroxy-2-oxo-1,2-dihydroquinoline were found during quinoline biodegradation. The presence of these intermediates suggested that at least two pathways were involved for quinoline degradation by Comamonas sp. and a reasonable degradation route was proposed to account for the intermediates observed. This revised version was published online in July 2006 with corrections to the Cover Date.     

Aerobic biodegradation characteristics and metabolic products of quinoline by a Pseudomonas strain

A bacterial strain, BW003, which utilized quinoline as its sole C, N and energy source, was isolated and identified as Pseudomonas sp. BW003 degraded 192–911 mg/l quinoline within 3–8 h with removal rates ranging from 96% to 98%. The optimum conditions for the degradation were 30 °C and pH 8. In the process of biodegradation, at least 43% of quinoline was transformed into 2-hydroxyquinoline, then 0.69% of 2-hydroxyquinoline was transformed into 2,8-dihydroxyquinoline, and then, presumably, into 8-hydroxycoumarin. Meanwhile, at least 48% of the nitrogen in quinoline was directly transformed into ammonia-N. An extra carbon source enhanced the nitrogen transformation from ammonia-N. Further experiments showed that, besides cell synthesis, BW003 transformed less than 6% of ammonia-N into nitrate through heterotrophic nitrification. In addition, BW003 contained a large plasmid, which may be involved in quinoline metabolism. The study indicates that quinoline and its metabolic products can be eliminated from wastewater by controlling the C/N ratio using BW003 as the bioaugmentation inoculum.     

Comparison of the mutagenicity of quinoline and all monohydroxyquinolines with a series of arene oxide, trans-dihydrodiol, diol epoxide, N-oxide and arene hydrate derivatives of quinoline in the Ames/Salmonella microsome test.

Fourteen new quinoline derivatives were synthesised and their mutagenicity compared in the Ames test using Salmonella typhimurium TA100 as indicator strain with and without (Aroclor-induced) S9 mix. None of the synthesised quinoline derivatives had to our knowledge been examined before in the Ames test. Quinoline and the monohydroxyquinolines were included as reference compounds. Three of the new derivatives, i.e., quinoline 7,8-oxide, N-methyl-quinoline 5,6-oxide and trans-quinoline-5,6,7,8-dioxide appeared to be mutagenic. Quinoline 7,8-oxide was positive only in the presence of S9 mix, the specific mutagenicity amounting to 2498 +/- 96 and 1289 +/- 120 revertants per mumole with 20 and 10% S9 in the mix, respectively. Both N-methyl-quinoline 5,6-oxide and trans-quinoline-5,6,7,8-dioxide were weakly positive, the former only in the presence of the S9 mix, and the latter irrespective of the presence of S9 mix, the specific mutagenicity amounting to 134 +/- 6 and 123 +/- 10 revertants per mumole, respectively. The mutagenic potency of quinoline 7,8-oxide was of the same order as that of quinoline itself and was distinctly lower than that of 8-hydroxyquinoline. Inconclusive results were obtained with trans-7,8-dihydroxy-7,8-dihydroquinoline, 5,6-dihydroxy-7,8-epoxy-5,6,7,8-tetrahydroquinoline and 8-hydroxyquinoline-N-oxide; if these compounds are mutagenic their mutagenic potency would be at least 20-30 times lower than that of the parent compounds. None of the other chemically synthesised quinoline derivatives showed mutagenic activity with TA100 either in the presence or in the absence of S9 mix. The results obtained with the reference compounds were in accordance with literature data.     

Microbial transformation of quinoline by a Pseudomonas sp.

A Pseudomonas sp. isolated from sewage by enrichment culture on quinoline metabolized this substrate by a novel pathway involving 8-hydroxycoumarin. During early growth of the organism on quinoline, 2-hydroxyquinoline accumulated as the intermediate; 8-hydroxycoumarin accumulated as the major metabolite on further incubation. 2,8-Dihydroxyquinoline and 2,3-dihydroxyphenylpropionic acid were identified as the other intermediates. Inhibition of quinoline metabolism by 1 mM sodium arsenite led to the accumulation of pyruvate, whereas inhibition by 5 mM arsenite resulted in the accumulation of 2-hydroxyquinoline as the major metabolite and 2,8-dihydroxyquinoline as the minor metabolite. Coumarin was not utilized as a growth substrate by this bacterium, but quinoline-grown cells converted it to 2-hydroxyphenylpropionic acid, which was not further metabolized. Quinoline, 2-hydroxyquinoline, 8-hydroxycoumarin, and 2,3-dihydroxyphenylpropionic acid were rapidly oxidized by quinoline-adapted cells, whereas 2,8-dihydroxyquinoline was oxidized very slowly. Quinoline catabolism in this Pseudomonas sp. is therefore initiated by hydroxylation(s) of the molecule followed by cleavage of the pyridine ring to yield 8-hydroxycoumarin, which is further metabolized via 2,3-dihydroxyphenylpropionic acid.     

Microbiological degradation of quinoline by Pseudomonas stutzeri: the coumarin pathway of quinoline catabolism

A Gram-negative, oxidase positive, polar flagellated rod, characterised as Pseudomonas stutzeri, has been isolated from sewage by enrichment culture on quinoline. The organism utilizes quinoline as the sole source of carbon, nitrogen and energy, and liberates UV absorbing and phenolic metabolites during its growth on quinoline. 2-Hydroxyquinoline, 2,8-dihydroxyquinoline, 8-hydroxycoumarin and 2,3-dihydroxyphenylpropionic acid have been isolated as the transformation products of quinoline by this bacterium. Quinoline, 2-hydroxyquinoline, and 8-hydroxycoumarin were rapidly oxidised by quinoline-adapted cells; 2,3-dihydroxyphenylpropionic acid oxidation was also demonstrated by Warburg respirometry but 2,8-dihydroxyquinoline was not oxidised. A pathway for quinoline catabolism by P. stutzeri and the probable mechanisms for formation of 8-hydroxycoumarin are suggested.     

Microbial transformation of quinoline by a Pseudomonas sp

A Pseudomonas sp. isolated from sewage by enrichment culture on quinoline metabolized this substrate by a novel pathway involving 8-hydroxycoumarin. During early growth of the organism on quinoline, 2-hydroxyquinoline accumulated as the intermediate; 8-hydroxycoumarin accumulated as the major metabolite on further incubation. 2,8-Dihydroxyquinoline and 2,3-dihydroxyphenylpropionic acid were identified as the other intermediates. Inhibition of quinoline metabolism by 1 mM sodium arsenite led to the accumulation of pyruvate, whereas inhibition by 5 mM arsenite resulted in the accumulation of 2-hydroxyquinoline as the major metabolite and 2,8-dihydroxyquinoline as the minor metabolite. Coumarin was not utilized as a growth substrate by this bacterium, but quinoline-grown cells converted it to 2-hydroxyphenylpropionic acid, which was not further metabolized. Quinoline, 2-hydroxyquinoline, 8-hydroxycoumarin, and 2,3-dihydroxyphenylpropionic acid were rapidly oxidized by quinoline-adapted cells, whereas 2,8-dihydroxyquinoline was oxidized very slowly. Quinoline catabolism in this Pseudomonas sp. is therefore initiated by hydroxylation(s) of the molecule followed by cleavage of the pyridine ring to yield 8-hydroxycoumarin, which is further metabolized via 2,3-dihydroxyphenylpropionic acid.     

Active site geometry and substrate recognition of the molybdenum hydroxylase quinoline 2-oxidoreductase

The soil bacterium Pseudomonas putida 86 uses quinoline as a sole source of carbon and energy. Quinoline 2-oxidoreductase (Qor) catalyzes the first metabolic step converting quinoline to 2-oxo-1,2-dihydroquinoline. Qor is a member of the molybdenum hydroxylases. The molybdenum ion is coordinated by two ene-dithiolate sulfur atoms, two oxo-ligands, and a catalytically crucial sulfido-ligand, whose position in the active site was controversial. The 1.8 A resolution crystal structure of Qor indicates that the sulfido-ligand occupies the equatorial position at the molybdenum ion. The structural comparison of Qor with the allopurinol-inhibited xanthine dehydrogenase from Rhodobacter capsulatus allows direct insight into the mechanism of substrate recognition and the identification of putative catalytic residues. The active site protein variants QorE743V and QorE743D were analyzed to assess the catalytic role of E743.     

反应器进水管生物膜中喹啉降解菌的分离鉴定及降解特性

【背景】喹啉是一类高毒、致癌且难降解的含氮杂环化合物,本实验室建立了一个长期高效运行的反硝化喹啉降解生物反应器。【目的】从反应器进水管富集的生物膜中筛选有氧条件下降解喹啉的菌株。【方法】通过以喹啉为唯一碳源的培养基来富集、分离、纯化菌株;利用16S rRNA基因的序列分析鉴定分离株的系统发育地位;比较不同pH及温度条件下菌株的喹啉降解特性。【结果】经鉴定,4株分离物Q1、Q3、Q7和Q8分别属于Sphingobium、Massilia、Rhodococcus和Dyadobacter属。降解实验表明,以上菌株均能在48 h内实现50 mg/L喹啉的完全去除,但各自表现出不同的降解特性,其中Q1、Q3和Q8在降解过程中都检测到了喹啉降解产物2-羟基喹啉的积累。降解喹啉的Sphingobium、Massilia和Dyadobacter属菌株尚未见报道。【结论】从喹啉降解生物反应器的进水管内分离的4株喹啉降解菌可为设计处理含喹啉工业废水的反应器提供新菌种资源,对于完善喹啉生物降解机理研究具有实际意义。     

Transformation of indole and quinoline by Desulfobacterium indolicum (DSM 3383)

Degradation of indole and quinoline by Desulfobacterium␣indolicum was studied in batch cultures. The first step in the degradation pathway of indole and quinoline was a hydroxylation at the 2 position to oxindole and 2-hydroxyquinoline respectively. These hydroxylation reactions followed saturation kinetics. The kinetic parameters for indole were an apparent maximum specific transformation rate (V _Amax) of 263 μmol mg total protein⁻¹ day⁻¹ and an apparent half-saturation constant (K _Am) of 139 μM. The V _Amax for quinoline was 170 μmol mg total protein⁻¹ day⁻¹ and K _Am was 92 μM. Oxindole inhibited indole hydroxylation whereas 2-hydroxyquinoline stimulated quinoline hydroxylation. An adaptation period of approximately 20 days was required before transformation of 2-hydroxyquinoline in cultures previously grown on quinoline. Indole and quinoline were hydroxylated with a lag phase shorter than 4 h in a culture adapted to ethanol. Chloramphenicol inhibited the hydroxylation of indole and quinoline in ethanol-adapted cells, indicating an inducible enzyme system. Chloramphenicol had no effect on the hydroxylation of indole in quinoline-adapted cells or on the hydroxylation of quinoline in indole-adapted cells. This indicated that it was the same inducible enzyme system that hydroxylated indole and quinoline. Received: 16 July 1996 / Received revision: 23 September 1996 / Accepted: 29 September 1996     

Microbial degradation of quinoline and methylquinolines.

Several bacterial cultures were isolated that are able to degrade quinoline and to transform or to degrade methylquinolines. The degradation of quinoline by strains of Pseudomonas aeruginosa QP and P. putida QP produced hydroxyquinolines, a transient pink compound, and other undetermined products. The quinoline-degrading strains of P. aeruginosa QP and P. putida QP hydroxylated a limited number of methylquinolines but could not degrade them, nor could they transform 2-methylquinoline, isoquinoline, or pyridine. Another pseudomonad, Pseudomonas sp. strain MQP, was isolated that could degrade 2-methylquinoline. P. aeruginosa QP was able to degrade or to transform quinoline and a few methylquinolines in a complex heterocyclic nitrogen-containing fraction of a shale oil. All of the quinoline- and methylquinoline-degrading strains have multiple plasmids including a common 250-kilobase plasmid. The 225-, 250-, and 320-kilobase plasmids of the P. aeruginosa QP strain all contained genes involved in quinoline metabolism.     

Molybdenum-dependent degradation of quinoline by Pseudomonas putida Chin IK and other aerobic bacteria

Eighteen different aerobic bacteria were isolated which utilized quinoline as sole source of carbon, nitrogen, and energy. Attempts were unsuccessful at isolating anaerobic quinoline-degrading bacteria. The optimal concentration of quinoline for growth was in the range of 2.5 to 5 mM. Some organisms excreted 2-hydroxyquinoline as the first intermediate. Hydroxylation of quinoline was catalyzed by a dehydrogenase which was induced in the presence of quinoline or 2-hydroxyquinoline. Quinoline dehydrogenase activity was dependent on the availability of molybdate in the growth medium. Growth on quinoline was inhibited by tungstate, an antagonist of molybdate. Partially purified quinoline dehydrogenase from Pseudomonas putida Chin IK indicated the presence of flavin, iron-sulfur centers, and molybdenum-binding pterin. M _r of quinoline dehydrogenase was about 300 kDa in all isolates investigated.Abbreviations APS ammonium peroxodisulfate - DCPIP 2,6-dichlorophenol-indophenol - EEO electroendosmosis - MTT thiazolyl blue - PES phenazine ethosulfate - TEMED N,N,N,N-tetramethyl-ethylenediamine     

Preparation and properties of matrix-supported horseradish peroxidase.

A new method of enzyme immobilization has been described using poly(4-methacryloxybenzoic acid) as the carrier. Activation of the polymer, prior to enzyme attachment, was achieved with N-ethoxycarbonyl-2-ethoxy-1,2-dihydroquinoline. The enzyme coupling step proceeded through nucleophilic attack by the protein on a mixed carbonic anhydride. The degree of polymer activation was determined by analysis for quinoline, a by-product of the reaction. The polymer-enzyme complex was compared to the enzyme in solution in terms of pH optimum, substrate kinetics, and thermal denaturation. Potential uses of the polymerenzyme system in chemical synthesis of benzoquinone derivatives are discussed.     

Microbial metabolism of quinoline and related compounds. VII. Quinoline oxidoreductase from Pseudomonas putida: a molybdenum-containing enzyme

The quinoline oxidoreductase from Pseudomonas putida was purified 50-fold to homogeneity with 21% recovery, using ammonium sulfate precipitation, hydrophobic interaction-, anion exchange-, and gel chromatography. The Mr of the native enzyme was calculated to be 300,000 by gel filtration. SDS-polyacrylamide gel electrophoresis of the enzyme revealed three protein bands corresponding to Mr 85,000, 30,000 and 20,000. The enzyme contained 8 atoms of iron, 8 atoms of acid-labile sulfide, 2 molecules of FAD, and the molybdenum cofactor, molybdopterin. Besides quinoline, the quinoline oxidoreductase also catalysed the conversion of 5-, 6-, 7- and 8-hydroxyquinoline and 8-chloroquinoline to the corresponding 2-oxo compounds. The incorporated oxygen atom was derived from water. Cyanide and methanol were effective inhibitors.     

Biotransformation of quinoline and methylquinolines in anoxic freshwater sediment

Quinoline (Q) and some isomers of methylquinoline (MQ) were transformed to hydroxylated products in freshwater sediment slurries incubated under methanogenic conditions at 25 °C. Methylquinoline transformation was not affected by a methyl group on the C-3 or C-4 carbon atom of the pyridine ring; 2-MQ, however, was not transformed. All isomers of dimethylquinoline (DMQ) tested (2,4-, 2,6-, 2,7-, and 2,8-DMQ) with a methyl group at the number 2 carbon also persisted in sediments after anaerobic incubation for one year at 25 °C.In most experiments, quinoline initially was transformed to 2-hydroxyquinoline (2-OH-Q), which was further metabolized to unidentified products. A second product, 4-CH₃-2-OH-Q, was detected in some experiments. This product accumulated and was not further transformed. 6-, 7-, and 8-Methylquinoline (6-, 7-, 8-MQ) were hydroxylated to form the respective 2-OH-MQ products. These hydroxylated products accumulated and were not further transformed. Hydroxylation of Q and 6-, 7- and 8-MQ at the 2-carbon position was confirmed by GC/FTIR and GC/MS analyses. The transformations of Q and MQs were pH dependent with an optimal pH of 7–8.The results of this study suggest that two pathways may exist for the anaerobic transformation of quinoline; one pathway leads to the formation of a hydroxylated intermediate and the other to a methylated and hydroxylated intermediate. In addition, our results suggest that a methyl substituent on the number 2 carbon inhibits the anaerobic transformation of quinoline derivatives.Abbreviations GC gas chromatography - GC/FTIR gas chromatography/Fourier transform infrared spectrometry - GC/MS gas chromatography/mass spectrometry - HPLC high performance liquid chromatography - MQ methylquinoline - Q quinoline     

π-Arene complexes.: Part 12. Synthesis of chromiumtricarbonyl complexes of quinoline and N-methylindoles and selected metallation reactions

The lithiation of indole, using a slight excess of n-butyl lithium in THF, followed by methylation and reaction with [Cr(CO)₆] in refluxing dibutyl ether, resulted in the formation of [Cr(η⁶-N-methylindole)(CO)₃] (1a) and [Cr(η⁶-N-methyl-2-methylindole)(CO)₃] (1b). In contrast, lithiation of quinoline in THF, silylation and the subsequent reaction with [Cr(CO)₆] under similar reaction conditions, afforded [Cr(η⁶-N-trimethylsilyl-2-butyl-1,2-dihydroquinoline)(CO)₃] (2) and [Cr(η⁶-{2-butyl-1,2,3,4-tetrahydroquinoline})(CO)₃] (3). The formation of [Cr(η⁶-2,2′-bis{N-methylindolyl})(CO)₃] (4) implied lithiation at the 2-position of 1a. However, metallation at the 7-position was also indicated during the same reaction. In the presence of [Mn(CO)₅Br], product 4 and the transmetallation product [Cr(η⁶-{7-(N-methylindolyl)Mn(CO)₅})(CO)₃] (5) were isolated. Reaction with titanocene dichloride gave [Cr(η⁶-{2-(N-methylindolyl)TiCp₂Cl})(CO)₃] (6), which slowly converted into [TiCp₂{Cr(η⁶-2-(N-methylindolyl)(CO)₃}₂] (7).     

Microbial degradation of quinoline and methylquinolines

Several bacterial cultures were isolated that are able to degrade quinoline and to transform or to degrade methylquinolines. The degradation of quinoline by strains of Pseudomonas aeruginosa QP and P. putida QP produced hydroxyquinolines, a transient pink compound, and other undetermined products. The quinoline-degrading strains of P. aeruginosa QP and P. putida QP hydroxylated a limited number of methylquinolines but could not degrade them, nor could they transform 2-methylquinoline, isoquinoline, or pyridine. Another pseudomonad, Pseudomonas sp. strain MQP, was isolated that could degrade 2-methylquinoline. P. aeruginosa QP was able to degrade or to transform quinoline and a few methylquinolines in a complex heterocyclic nitrogen-containing fraction of a shale oil. All of the quinoline- and methylquinoline-degrading strains have multiple plasmids including a common 250-kilobase plasmid. The 225-, 250-, and 320-kilobase plasmids of the P. aeruginosa QP strain all contained genes involved in quinoline metabolism.     

Simultaneous biodegradation of pyridine and quinoline by two mixed bacterial strains

Experiments were conducted to provide data on the effectiveness of bioaugmentation in the removal of pyridine and quinoline from different wastewaters. A pyridine-degrading bacterial strain (Paracoccus sp. BW001) and a quinoline-degrading strain (Pseudomonas sp. BW003) were isolated from the activated sludge of a coking wastewater treatment plant. In this study, a consortium of these two bacterial strains was used as inoculum to simultaneously degrade pyridine and quinoline in three types of wastewaters: sterile synthetic, domestic, and industrial. In addition, variation of the bacterial community structures during degradation was monitored by denaturing gradient gel electrophoresis and amplicon length heterogeneity polymerase chain reaction techniques. The results of our experiments indicate that pyridine and quinoline can be removed efficiently using this inoculum but that the degradation process results in the production of ammonium as a by-product. Also, in the two actual wastewaters investigated, we observed that several autochthonous strains of bacteria in both the domestic and industrial wastewater were tolerant of pyridine and quinoline and grew rapidly.     

Microbial metabolism of quinoline and related compounds. XI. Degradation of quinoline-4-carboxylic acid by Microbacterium sp. H2, Agrobacterium sp. 1B and Pimelobacter simplex 4B and 5B.

From soil enrichment cultures four strains, using quinoline-4-carboxylic acid as sole source of energy and carbon, have been isolated. According to their physiological properties these bacteria have been identified as Microbacterium sp. designated H2, as Agrobacterium sp. designated 1b and Pimelobacter simplex designated 4B and 5B. Metabolites of the degradation pathway of quinoline-4-carboxylic acid have been isolated and identified. With Pimelobacter simplex 4B and 5B 2-oxo-1,2-dihydroquinoline-4-carboxylic acid and 8-hydroxycoumarin-4-carboxylic acid were isolated. The Agrobacterium strain accumulated 2-oxo-1,2-dihydroquinoline-4-carboxylic acid and 2-oxo-1,2,3,4-tetrahydroquinoline-4-carboxylic acid in the media during growth; with Microbacterium sp. H2 we only found 8-hydroxycoumarin-4-carboxylic acid. With mutants of Microbacterium sp. H2 which were induced with N-methyl-N'-nitro-N-nitrosoguanidine we found 2-oxo-1,2-dihydroquinoline-4-carboxylic acid, 8-hydroxy-coumarin-4-carboxylic acid and 2,3-dihydroxyphenyl-succinic acid.     

Cry1Fa对Cry1Ac抗性棉铃虫的毒力评价

为了防治多种鳞翅目害虫, 表达Cry1Fa的转基因玉米和棉花已在美国商业化种植。明确棉铃虫Helicoverpa armigera对Cry1Fa与Cry1Ac的交互抗性及这两种杀虫蛋白之间的协同作用, 可以为表达 Cry1Fa+Cry1Ac的转双价抗虫棉花的合理应用提供依据。本实验测定了Cry1Fa对棉铃虫敏感品系（96S）及用Cry1Ac筛选的抗性品系（BtR, 抗性倍数2 194.15倍）的毒力, 发现Cry1Fa对敏感棉铃虫的毒力远低于Cry1Ac, LC₅₀值是Cry1Ac的504.80倍; 而且抗性品系BtR对Cry1Fa存在19.98倍的交互抗性。Cry1Fa与Cry1Ac混用可以提高Cry1Fa毒杀敏感棉铃虫的效果, 尤其是Cry1Fa浓度较低时, 加入Cry1Ac, 可以显著增加Cry1Fa的毒力; 但只有加入较高浓度的Cry1Fa时才能增加Cry1Ac的毒力。由于BtR品系已经对Cry1Ac产生抗性, Cry1Ac对抗性棉铃虫的毒力明显降低; 在较高浓度的Cry1Ac中加入Cry1Fa可以显著增加棉铃虫的死亡率（P=0.0015, F=6.88, df=6）, 但最高死亡率仅为58.33%。D-饱和最优试验的结果证实, Cry1Ac对于敏感棉铃虫的死亡率的影响达到显著水平（t₁=13.76﹥t_0.05）, Cry1Ac与Cry1Fa的交互作用对毒力的影响也达到显著水平（t₂₂=2.42﹥t_0.05; t₁₁=6.95﹥t_0.05; t₁₂=3.43﹥t_0.05）。Cry1Ac和Cry1Fa对抗性棉铃虫死亡率的影响都达到显著水平（t₁=3.03﹥t_0.05;t₂=2.59﹥t_0.05）, 但Cry1Ac是决定抗、 感棉铃虫死亡率的关键因素; Cry1Ac与Cry1Fa最佳浓度配比范围都是1.41~2.10 μg/cm2; 在抗性品系中, Cry1Ac和Cry1Fa的交互作用不显著。所以, 尽管Cry1F+Cry1A作物扩大了杀虫谱, 但棉铃虫对这两种蛋白存在交互抗性, 而且这两种蛋白混用对治理抗Cry1Ac棉铃虫的效果不理想, 因此不建议在中国种植表达Cry1F+Cry1A的棉花。关