Abstract
Background
Studies investigating the association between pesticide exposure and colorectal cancer (CRC) risk have been inconclusive.
Objectives
Investigate the association between pesticide exposure and CRC risk through a systematic literature review.
Methods
CRC has the fourth-highest rate of cancer-caused death in the US after lung cancer, breast cancer in women, and prostate cancer in men. Here we have conducted a systematic literature search on studies examining the association between any pesticide exposure and CRC risk using PubMed, MEDLINE via EBSCO host, and Embase according to the Preferred Reporting Items for Systematic Reviews and Meta-Analyses checklist.
Results
Following the review, 139 articles were included for qualitative evaluation. Study participants were farmers, pesticide applicators, pesticide manufacturers, spouses of pesticide applicators, farm residents, Korean veterans of the Vietnam War, rural communities, and those who consumed food with pesticide residues. The studies’ results were split between those with significant positive (39 significant results) and inverse (41 significant results) associations when comparing pesticide exposure and CRC risk.
Discussion
From our literature review, we have identified a similar number of significant positive and inverse associations of pesticide exposure with CRC risk and therefore cannot conclude whether pesticide exposure has a positive or inverse association with CRC risk overall. However, certain pesticides such as terbufos, dicamba, trifluralin, S-ethyl dipropylthiocarbamate (EPTC), imazethapyr, chlorpyrifos, carbaryl, pendimethalin, and acetochlor are of great concern not only for their associated elevated risk of CRC, but also for the current legal usage in the United States (US). Aldicarb and dieldrin are of moderate concern for the positive associations with CRC risk, and also for the illegal usage or the detection on imported food products even though they have been banned in the US. Pesticides can linger in the soil, water, and air for weeks to years and, therefore, can lead to exposure to farmers, manufacturing workers, and those living in rural communities near these farms and factories. Approximately 60 million people in the US live in rural areas and all of the CRC mortality hotspots are within the rural communities. The CRC mortality rate is still increasing in the rural regions despite the overall decreasing of incidence and mortality of CRC elsewhere. Therefore, the results from this study on the relationship between pesticide exposure and CRC risk will help us to understand CRC health disparities.
Keywords: colorectal cancer, pesticides, environmental exposure, occupational exposure
1. Introduction
Cancer is the second leading cause of death in the United States (US) following heart disease (ACS, 2019), and colorectal cancer (CRC) is the second leading cause of cancer-related deaths in the US (ACS, 2019). Like many other cancer types, there are some genetic mutations associated with CRC. However, more than half (55%) of CRC in the US are attributable to modifiable risk factors such as diet, lifestyle factors, and co-morbidities that can promote intestinal inflammation and facilitate polyp growth (ACS, 2019). Some of these include heavy alcohol consumption (average of greater than three drinks a day) (McNabb et al., 2020), smoking (Carter et al., 2015), red and processed meat consumption (Vieira et al., 2017), physical inactivity (Boyle et al., 2012), obesity (Xue et al., 2017), and type 2 diabetes (Ma et al., 2018). These lifestyle choices and co-morbidities are highly correlated with socioeconomic status. Additionally, education level, occupation, and income affecting living environment and access to resources also contribute to cancer risk (ACS, 2021).
One factor that has been studied and shown to be correlated to CRC risk, in some cases, is exposure to substances that are meant to control pests. In this review, these substances will be referred to as pesticides, but this definition also includes other pest repellent substances such as herbicides, insecticides, fungicides, and many others (EPA, 2020). Pesticide exposure can result from a related occupation such as farming (Ilgaz and Gozum, 2018; Salerno et al., 2016; Settimi et al., 2001), pesticide application (Alexander et al., 2012; Cantor and Silberman, 1999; Greenburg et al., 2008; Hou et al., 2006; Lee et al., 2004b; Lynch et al., 2006; Rusiecki et al., 2006), and pesticide manufacturing (Acquavella et al., 1996; Leet et al., 1996; Wilkinson et al., 1997). Additionally, spouses of farmers (Deziel et al., 2019), those living in rural areas (Wang et al., 2002), those who eat non-organic foods (Baudry et al., 2018; Callahan et al., 2017), or those who apply or have pesticides applied to their yards can also be exposed (Su et al., 2016).
Pesticides that are applied to farms or yards can remain in the environment for longer than intended. Sometimes pesticides either sit on top of the soil (surface soil) and therefore spread via dust, runoff, or leach through the soil (parent soil) and thus reach the groundwater and, in some cases, drinking water (Sjerps et al., 2019; Sultana et al., 2018; Xu et al., 2018). Some studies have found pesticides, such as neonicotinoids, remain in the dust and soil at least one year following the previous planting season. These pesticides were an order of magnitude higher in concentration on the surface soil than the parent soil (Limay-Rios et al., 2016). Another pesticide, fipronil, is a phenylpyrazole insecticide that disrupts the insect’s central nervous system by blocking chloride channels. Similar to the neonicotinoids, it was found that degradation products of fipronil were three to nine times higher in dust than in soil and therefore were also detected in runoff samples (Cryder et al., 2019). Another study has found that pesticides such as 2-methyl-4-chlorophenoxyacetic acid (MCPA) leach more from frozen vs. unfrozen topsoil (Holten et al., 2018).
Most of the scientific articles identified have analyzed the association between pesticide exposure and colon cancer, rectal cancer, or CRC risk using epidemiological methods as compared to studies that measured the level or concentration of pesticides in the biological samples. Epidemiological methods have limitations mainly because they rely on self-reporting, whereas biological sample measurement studies analyze specific or multiple pesticide metabolites in human samples. Samples from stool, colon wash, colon tissue, or polyps are optimal to study the association with colon or rectal cancer risk. In this review, we were only able to identify biological sample measurement studies that measured pesticide levels in serum samples.
Several review papers have previously looked into the associations between pesticide exposure and cancer risk (Acquavella et al., 1998; Alavanja and Bonner, 2012; Alexander et al., 2012; Blair and Freeman, 2009; Blair et al., 1985a; Blair et al., 1992; Burns, 2005; Oddone et al., 2014; Weichenthal et al., 2010), but only two specifically focused on CRC only and no other cancers (Alexander et al., 2012; Oddone et al., 2014) while the others looked at cancer more broadly or various types of cancer (Acquavella et al., 1998; Alavanja and Bonner, 2012; Blair and Freeman, 2009; Blair et al., 1985a; Blair et al., 1992; Burns, 2005; Weichenthal et al., 2012). In addition, only one third (three out of nine) of the review papers looked at the association between certain pesticide exposures and cancer risks including CRC risk (Alavanja and Bonner, 2012; Alexander et al., 2012; Weichenthal et al., 2010) while the rest more generally looked at pesticide exposure among different occupations or environmental risk factors (farmers, pesticide applicators, agricultural populations, and crop and animal production) and the association with cancer risk including CRC instead of the effect of specific pesticide exposure or the effect of specific pesticide exposure on the risk of other cancer types (Acquavella et al., 1998; Alexander et al., 2012; Blair and Freeman, 2009; Blair et al., 1985a; Burns, 2005; Oddone et al., 2014). The three review papers that looked at the association between certain pesticide exposure and CRC risk (Alavanja and Bonner, 2012; Alexander et al., 2012; Weichenthal et al., 2010) found six pesticides including aldicarb (Lee et al., 2007b), dicamba (Samanic et al., 2006), S-ethyl dipropylthiocarbamate; EPTC (van Bemmel et al., 2008), imazethapyr (Koutros et al., 2009), trifluralin (Kang et al., 2008), and fonofos (Lee et al., 2007b) with significant positive associations with colon cancer risk, five pesticides including chlordane (Purdue et al., 2007), chlorpyrifos (Lee et al., 2004a; Lee et al., 2007b), pendimethalin (Hou et al., 2006), toxaphene (Lee et al., 2007b), and carbaryl (Lee et al., 2007b) with significant positive associations with rectal cancer risk, and only one pesticide, 2,4-dichlorophenoxyacetic acid; 2,4-D, with a significant inverse association with colon cancer risk (Lee et al., 2007b). The remaining review papers that more generally looked at the association between occupational or environmental exposure to pesticides and CRC risk found that farmers, crop and animal production, and agricultural populations showed mostly significant inverse associations with colon cancer, rectal cancer, or CRC risk (Acquavella et al., 1998; Alexander et al., 2012; Blair and Freeman, 2009; Blair et al., 1985a; Oddone et al., 2014).
There have also been some research studies that suggest some pesticides, such as Metarhizium anisopliae (Dornetshuber-Fleiss et al., 2013), deguelin (Murillo et al., 2003; Murillo et al., 2002), oryzalin (Powis et al., 1997), benzimidazole carbamates (Wales et al., 2015), rotenone (Yoshitani et al., 2001), and thujone (Zhou et al., 2016) are anti-carcinogenic. Additionally, studies have shown a lower incidence of CRC in farmers compared to the general population (Garabrant et al., 1984). This has been attributed to factors such as lower smoking rates and higher physical activity (Garabrant et al., 1984).
Below we discussed groups of pesticides and individual pesticides that have been shown to have significant associations with colon cancer, rectal cancer, or CRC risk. We have discussed the results of previous studies showing the persistence of these pesticides in the environment and in organisms, including humans, as well as some of the reported health issues associated with exposure to these pesticides.
Insecticides are pesticides that have various methods of action to kill insects considered to be pests. Organochlorine insecticides (OCIs) have been used globally and across the US and many have been shown to be persistent in the environment and in organisms. Some examples of OCIs include dichlorodiphenyltrichloroethane (DDT), heptachlor, lindane, chlordane, and toxaphene. DDT opens sodium channels in neurons, causing the sodium channels to spontaneously fire and subsequently leads to spasms and death (Dong, 2007). Lindane is an insecticidal neurotoxin that interferes with gamma-aminobutyric acid (Hall and Hall, 1999; Narahashi, 2002; Sunol et al., 1989). Chlordane is environmentally resistant to degradation and bioaccumulates and is toxic to humans and the environment (EPA, 1994). Heptachlor persists in the environment for many years and can be detected in human blood, fat, and tissue when exposed (CDC, 1993). Toxaphene remains in the soil for 1 to 14 years without degrading (EPA, 1996). Another group of insecticides are organophosphate insecticides (OPIs) and some such as tebufos have been shown to be associated with various cancers (Lerro et al., 2015a). Carbamate insecticides reversibly inhibit acetylcholinesterase, and therefore affect the nervous system leading to neurotoxic effects (Fukuto, 1990). Three examples of carbamate insecticides are butylate, carbaryl, and aldicarb. Butylate is used specifically for corn crops and along with carbaryl is not believed to cause cancer in humans (EPA, 1993; HSDB, 1993), while aldicarb is believed to be linked to cancer (EPA, 2002).
Another type of pesticide which is used to kill plants such as weeds that are considered harmful to the agricultural product of interest are called herbicides. Some chlorophenoxy herbicides such as 2,4-D and MCPA are growth regulators (Grossmann, 2010) and degrade in soil (Helweg, 1987; NPIC, 2008) but they have been shown to cause health problems in humans. Some of these health problems include severe eye irritations (EPA, 2004, 2005) and 2,4-D has been shown to potentially cause fertility problems in men (Tan et al., 2016), and the World Health Organization (WHO) has classified 2,4-D as a possible carcinogen (WHO, 2020). Another chlorophenoxy herbicide is dicamba which functions by causing weeds to grow beyond their nutrient supply and can become airborne and cause damage to nearby fields (Bunch et al., 2012). Anilide/ aniline herbicides are another group of herbicides and some examples include acetochlor, alachlor, pendimethalin, and trifluralin. Trifluralin interrupts mitosis to prevent root development (Senseman, 2007) and is toxic to aquatic life (Harrahy, 2003b). Pendimethalin inhibits cell elongation and division (EPA, 2007) and can increase the risk of developing pancreatic cancer (Andreotti et al., 2009). Additionally, acetochlor and alachlor are also herbicides that inhibit cell elongation. Acetochlor has effects on aquatic life (Harrahy, 2003a) and is classified as a probable human carcinogen (WHO, 2020). Alachlor causes slight eye and skin irritation (EPA, 1998) and has been detected in drinking water (Barbosa et al., 2016). EPTC is a thiocarbamate herbicide that inhibits the formation of cuticles in the early growth of seedlings and can cause neurotoxic effects such as neuronal degradation or necrosis in rats and dogs (EPA, 1999).
We have included colon cancer, rectal cancer, and CRC in this literature review and separated the discussions because some articles analyzed colon and rectal cancer separately while others grouped them together in what is commonly called colorectal cancer (CRC). This review included 139 research articles analyzing 56 different pesticides.
We will also discuss the bans, use, detection on imported food, and hazards of these 56 pesticides reviewed, which are summarized in Table 1. Ten of these 56 pesticides have not been banned anywhere, as reported by the Pesticide Action Network International (PAN) (PAN, 2020) and by Donley et al. 2019 (Donley, 2019). Five of these ten pesticides that are not banned anywhere (Donley, 2019; PAN, 2020) are classified as hazardous by WHO (WHO, 2019) including dicamba, glyphosate, metolachlor, metribuzin, and ziram. Of these 56 pesticides, 31 have been banned by the European Union (EU) and United Kingdom (UK) along with other countries (Donley, 2019; PAN, 2020), 23 of which have been classified as hazardous by WHO (WHO, 2019). Of these 56 pesticides, 17 have been banned or not approved in the US (Donley, 2019; PAN, 2020), 12 of which are classified as hazardous by WHO (WHO, 2019). In addition, 23 out of these 56 pesticides have been detected on imported food by the U. S. Food and Drug Administration (FDA) as of 2018 (FDA, 2018), including 4 which have been banned in the US (Donley, 2019; PAN, 2020) and 18 that the WHO have reported as slightly to extremely hazardous (WHO, 2019).
Table 1.
Pesticide Bans by Country, Hazards, Use, and Detection in Imported Foods.
Pesticide | Hazard rating (WHO)1 | Number of countries banned (PAN)2, Donley 20193 | Used in USA as of 2017 (USGS)4 | Detected on imported foods as of 2018 (FDA)5 |
---|---|---|---|---|
2,4-D | moderately hazardous | 3 (Mozambique, Norway, Vietnam) | x | x |
2,4,5-T | 1 US | |||
2,4,5-TP | 0 | |||
acetochlor | slightly hazardous | 38 (EU 27, UK + 10 others) | x | |
alachlor | moderately hazardous | 95 (US, EU 27, UK + 66 others) | x | |
aldicarb | extremely hazardous | 104 (US, EU 27, UK + 75 others) | x | |
aldrin | 1 US | |||
aluminium phosphide | 1 (China) | |||
atrazine | slightly hazardous | 37 (EU 27, UK + 9 others) | x | x |
benomyl | 35 (US, EU 27, UK + 6 others) | |||
butylate | Slightly hazardous | 30 (US, EU 27, UK, Brazil) | ||
captan | 6 (Cambodia, Fiji, Guinea, Oman, Saudi Arabia, Vietnam) | x | x | |
carbaryl | moderately hazardous | 35 (EU 27, UK + 7 others) | x | x |
carbofuran | highly hazardous | 64 (US, EU 27, UK + 35 others) | x | |
carbon disulfide | 0 | |||
carbon tetrachloride | 31 (EU 27, UK, Brazil, Switzerland, Thailand) | |||
chlordane | moderately hazardous | 142 (US, EU 27, UK + 113 others) | x | |
chlorimuronethyl | 0 | |||
chlorothalonil | 3 (Colombia, Palestine, Saudi Arabia) | x | x | |
chlorpyrifos | moderately hazardous | 4 (Palestine, Saudi Arabia, Sri Lanka, Vietnam) | x | x |
coumaphos | highly hazardous | 30 (EU 27, UK, Cambodia, China) | x | |
cyanazine | moderately hazardous | 30 (US, EU 27, UK, Oman) | ||
DDT | moderately hazardous | 136 (US, EU 27, UK + 107 others) | x | |
diazinon | moderately hazardous | 32 (EU 27, UK, Argentina, India, Mozambique, Palestine) | x | x |
dicamba | moderately hazardous | 0 | x | |
dichlorvos | highly hazardous | 33 (EU 27, UK + 5 others) | x | |
dieldrin | 1 US | x | ||
EPTC | moderately hazardous | 29 (EU 27, UK, Brazil) | x | |
ethylene dibromide | 124 (EU 27, UK + 96 others) | |||
fonofos | 34 (US, EU 27, UK + 5 others) | |||
glyphosate | slightly hazardous | 0 | x | x |
heptachlor | 1 US | |||
hexachloro benzene | extremely hazardous | 129 (US, EU 27, UK + 100 others) | ||
imazethapyr | 29 (EU 27, UK, Norway) | x | x | |
lindane | moderately hazardous | 121 (US, EU 27, UK + 92 others) | ||
malathion | slightly hazardous | 2 (Palestine, Syria) | x | x |
mancozeb | 1 (Saudi Arabia) | x | ||
maneb | 30 (US, EU 27, UK, Brazil) | |||
MCPA | moderately hazardous | 2 (Cambodia, Thailand) | x | |
metalaxyl | moderately hazardous | 1 (Brazil) | x | x |
methyl bromide | 35 (EU 27, UK + 7 others) | |||
metolachlor | slightly hazardous | 0 | x | x |
metribuzin | moderately hazardous | 0 | x | x |
paraquat | moderately hazardous | 46 (EU 27, UK + 18 others) | x | |
parathion (ethyl) | extremely hazardous | 114 (US, EU 27, UK + 85 others) | ||
pendimethalin | moderately hazardous | 1 (Norway) | x | x |
pentachloro phenol | highly hazardous | 114 (US, EU 27, UK + 85 others) | ||
permethrin | moderately hazardous | 29 (EU 27, UK, Syria) | x | x |
petroleum oil | 0 | x | ||
phorate | extremely hazardous | 38 (EU 27, UK + 10 others) | x | x |
terbufos | extremely hazardous | 34 (EU 27, UK + 6 others) | x | |
tetrachloro phenol | 0 | |||
toxaphene | 1 US | |||
trichlorfon | moderately hazardous | 53 (US, EU 27, UK + 24 others) | ||
trifluralin | 28 (EU 27, UK) | x | x | |
ziram | moderately hazardous | 0 | x |
World Health Organization (WHO) Recommended Classification of Pesticides by Hazard and Guidelines to Classification 2019 (WHO, 2019),
Pesticide Action Network (PAN) International Consolidated List of Banned Pesticides, October 20, 2020 (PAN, 2020),
United States Geological Survey (USGS) Pesticide National Synthesis Project, Estimated Annual Agricultural Pesticide Use, Archived preliminary county level pesticide use estimates, 2017 (USGS, 2017),
U.S. Food and Drug Administration (FDA) Pesticide Residue Monitoring Program Fiscal Year 2018 Pesticide Report (FDA, 2018).
The relationship between pesticide exposure and CRC risk is of particular interest to understand CRC health disparities. Therefore, this systematic review aimed to investigate the association between human pesticide exposure and CRC risk and incidence. We hypothesized that those exposed to pesticides would have a higher risk and incidence of CRC.
2. Methods
2.1. Literature Search
This systematic, qualitative review was performed according to the Preferred Reporting Items for Systematic Reviews and Meta-Analyses (PRISMA) checklist and flow diagram (Moher et al., 2009). We systematically searched PubMed, MEDLINE via EBSCO host, and Embase for research articles that examined the association between human pesticide exposure and colon cancer, rectal cancer, or CRC risk and incidence. We used the terms colon cancer, rectal cancer, and CRC because different articles specifically examined colon and rectal cancer separately, while others grouped the two into colorectal cancer (CRC). We used the term pesticide broadly to include pesticides, herbicides, insecticides, and other pest deterrents such as fumigants. We performed a broad literature search and did not restrict our search any further based on certain pesticides, insecticides, herbicides, or groups. The bibliographic search was performed in February 2020 and encompassed the available literature up to that time. The following search terms were used: (colorectal OR colon) AND cancer AND (pesticide OR herbicide OR insecticide). An English language filter was applied because of the lack of translation resources. All original articles found on the topic were epidemiological studies or biological sample measurement studies, and only those involving humans were included. All cell culture and animal studies were excluded. Figure 1 is a flow diagram illustrating this literature review process. Odds ratio (OR), relative risk/risk ratio (RR), hazard ratio (HR), standardized incidence ratio (SIR), standardized mortality ratio (SMR), standardized risk ratio (SRR), proportionate mortality ratio (PMR), proportionate cancer mortality ratio (PCMR), mortality odds ratio (MOR), confidence interval (CI), p-trend, and p-value were primary endpoints for the epidemiological studies and mean abundance/ level/ concentration and p-value were primary endpoints for the biological sample measurement studies. We did not calculate these primary endpoints; they were calculated in these primary studies that we are reviewing. Epidemiological effect sizes report a number, which denotes the strength of the association of the specific exposure on the outcome, which in this case is the association of the pesticide exposure on the CRC risk. Explained more simply, a positive association can mean that an increased level of the exposure (or presence of an exposure vs. no exposure) has resulted in an increased risk of the outcome. Our intention is to determine if there is an overall association between pesticide exposure and colon cancer, rectal cancer, and CRC risk, discuss this association, and discuss which certain pesticides or pesticide groups seem to be of most concern.
Figure 1.
Preferred Reporting for Systematic Review and Meta-Analyses Flow Diagram Modified from the PRISMA Group Source.
2.2. Eligibility Criteria
For this systematic analysis, the eligibility criteria included human epidemiology or human biological sample measurement studies researching the association (effect size, confidence interval, p-trend, and p-value or abundance and p-value) between pesticide exposure and colon cancer, rectal cancer, or CRC risk, incidence, or mortality. We were primarily focused on comparing the risk associated with occupations such as farming, pesticide application, and manufacturing. The abstracts were manually screened for relevance.
2.3. Data Collection Process
The data collection process was performed manually, and for studies that were deemed relevant, we saved the citation information, abstract, and article in a portable document format (PDF). For epidemiological studies, the data of interest were overall conclusions of association, correlation or statistical significance, OR, RR, HR, SIR, SMR, SRR, PMR, PCMR, MOR, 95% CI, and/or p-values/p-trends, and for biological sample measurement studies, the data of interest were abundance/ level/ concentration and p-value. Significant results were defined as those with a p-value or p-trend less than 0.05 or an effect size greater than or less than 1 with a confidence interval that does not include 1. For biological sample measurement studies the mean abundances/ levels/ concentrations were divided (cancer/ control) to determine the fold change. Study results were then described as positively (effect size or fold change greater than 1) or inversely associated (effect size or fold change less than 1) and significant depending on the confidence interval, p-value or p-trend. For our purposes, we will group the level of positive or inverse association for the epidemiological studies calculated from 1–10% disease rate of the non-exposed group for Cohen’s d of 0.2 as small, 0.5 as medium, and 0.8 as large associations (Cohen, 1988). Based on Cohen et al., we defined the effect sizes of the epidemiological studies as small positive associations ranging from 1.01–1.68, medium positive associations 1.69–3.50, and large positive associations 3.51 and up, whereas small inverse associations ranging from 0.99–0.59, medium inverse associations 0.58–0.28, and large inverse associations 0.27–0.01. Study results were then ranked into levels of concern based on the resulting association, statistical significance, and pesticide use and detection in the US. Pesticide results showing low concern involve pesticides already banned in the US or those that show inverse or no association with colon cancer, rectal cancer or CRC risk. Pesticides of moderate concern show (1) positive association with these types of cancers, are considered banned in the US but have been shown to be used as recently as 2017 or are still detectable in imported produce as of 2018; (2) pesticides in which studies have reported inconsistent results (positive in one study and inverse in another); or (3) pesticides shown to have small positive associations with these types of cancer that have not been banned in the US. Finally, pesticides of high concern are those that have been reported to have medium or large positive associations with these types of cancers and that have not been banned in the US.
3. Results and Discussion
3.1. Study Selection, Population, and Characteristics
Overall, we identified 139 studies for qualitative analysis (Table 2–6 and Figure 1). The systematic review was comprised of studies of farmers, pesticide applicators, pesticide manufacturing workers, pest-control workers, spouses of farmers, farm residents, rural populations, Korean Veterans who fought in the Vietnam war, people who ate food that may contain pesticide residues, and controls. Not all studies separated the participants by specialty; therefore, the term farmer is used more broadly. The studies were from 21 countries, including the US, Brazil, Egypt, Korea, Italy, Turkey, Spain, France, Iceland, Israel, Denmark, Germany, New Zealand, the UK, the Netherlands, Canada, Australia, Costa Rica, Sweden, Finland, and Iran. The publication dates of these studies included spanned 70 years (ranging from 1949 to 2019).
Table 2.
Associations Between Pesticide Exposure and Colon Cancer Risk.
Type | Group | Pesticide | Effect size summary | Reference |
---|---|---|---|---|
Insecticides | Organochlorine | Chlordane | RR 1.42 (0.87–2.32)* | Louis et al. 2017(Louis et al., 2017) |
OR 0.7 (0.5–1.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Heptachlor | RR 1.24 (0.46–3.36)* | Louis et al. 2017(Louis et al., 2017) | ||
OR 0.8 (0.5–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Aldrin | RR 1.73 (0.76–3.91)* | Louis et al. 2017(Louis et al., 2017) | ||
IWLED RR 0.4 (0.2–1.0) p-trend 0.04^ | Purdue et al. 2007(Purdue et al., 2007) | |||
OR 0.6 (0.4–1.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Dieldrin | RR 2.41 (0.89–6.53)* | Louis et al. 2017(Louis et al., 2017) | ||
OR 0.7 (0.4–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Aldrin and Dieldrin | SMR 1.40 (0.38–3.57)*^ | van Amelsvoort et al. 2009(van Amelsvoort et al., 2009) | ||
Toxaphene | RR 1.31 (0.42–4.12)* | Louis et al. 2017(Louis et al., 2017) | ||
OR 1.1 (0.7–1.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Pentachlorophenol and Tetrachlorophenol | SMR 1.00 (0.83–1.18), SIR 0.94 (0.81–1.09)* | Demers et al. 2006(Demers et al., 2006) | ||
DDT | PMR 0.23 (0.03–0.84)*^ | Cocco et al. 1997(Cocco et al., 1997) | ||
RR 1.17 (0.70–1.95)* | Louis et al. 2017(Louis et al., 2017) | |||
OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Lindane (gamma HCH) | RR 0.79 (0.25–2.49)* | Louis et al. 2017(Louis et al., 2017) | ||
male SIR 0.58 (0.47–0.70), female SIR 0.84 (0.36–1.65)* | Rafnsson 2006(Rafnsson, 2006) | |||
OR 0.7 (0.4–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Carbon tetrachloride/carbon disulfide | OR 0.8 (0.4–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Organophosphate | Trichlorfon | OR 1.5 (0.4–6.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Dichlorovos | RR 1.48 (0.78–2.80) p-trend 0.25 | Koutros et al. 2008(Koutros et al., 2008) | ||
OR 1.5 (0.9–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Chlorpyrifos | RR 0.72 (0.48–1.07)* | Lee et al. 2004a(Lee et al., 2004a) | ||
OR 0.8 (0.5–1.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Terbufos | T1 vs. T3 HR 1.77 (1.01–3.01) p-trend 0.009 | Bonner et al. 2010(Bonner et al., 2010) | ||
OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Fonofos | RR 1.66 (0.92–3.03) p-trend 0.14 | Mahajan et al. 2006(Mahajan et al., 2006a) | ||
0 vs. T3 OR 2.4 (1.2–4.8) p trend 0.105, OR 1.5 (1.0–2.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Malathion | OR 0.8 (0.5–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Parathion | OR 0.9 (0.6–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Phorate | 0 vs. T4 RR 1.07 (0.49–2.52) p-trend 0.74, T1 vs. T4 RR 2.48 (0.84–7.36) p-trend 0.18 | Mahajan et al. 2006(Mahajan et al., 2006b) | ||
OR 1.2 (0.8–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Coumaphos | OR 1.0 (0.6–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Diazinion | OR 0.7 (0.5–1.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Carbamate | Aldicarb | 0 vs. T2 OR 5.2 (1.5–18.1) p trend 0.008, OR 2.1 (1.3–3.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Carbofuran | RR 1.34 (0.54–3.31) p-trend 0.68 | Bonner et al. 2005(Bonner et al., 2005) | ||
OR 1.0 (0.7–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Carbaryl | RR 0.80 (0.30–2.14) p-trend 0.62 | Mahajan et al. 2007(Mahajan et al., 2007) | ||
OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Butylate | IWLED RR 0.35 (0.13–0.94) p-value<0.05 p-trend 0.04 | Lynch et al. 2009(Lynch et al., 2009) | ||
OR 0.9 (0.7–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Maneb/mancozeb | OR 0.7 (0.4–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Ziram | OR 0.7 (0.2–2.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Pyrethroid | Permethrin | LED RR 1.32 (0.75–2.34) p-trend 0.91 | Rusiecki et al. 2009(Rusiecki et al., 2009) | |
crops OR 0.9 (0.5–1.5), livestock OR 1.4 (0.9–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Organobromine | Ethylene dibromide | OR 0.6 (0.2–1.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Other | Petroleum oil | OR 0.9 (0.7–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Herbicides | Chlorophenoxy | 2,4,5-TP | OR 0.6 (0.3–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) |
2,4,5-T | OR 0.8 (0.6–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
2,4-D | SIR 0.95 (0.55–1.55)* | Burns et al. 2011(Burns et al., 2011) | ||
0 vs. T3 OR 0.4 (0.2–0.8) p trend 0.011^, OR 0.6 (0.4–0.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
2,4-D and MCPA | white men SRR 0.98 (0.88–1.09)*, white women SRR 0.99 (0.88–1.12)* | Schreinemachers 2000(Schreinemachers, 2000) | ||
Dicamba | LED T1 vs. T4 RR 3.29 (1.40–7.73) p-trend 0.02 | Samanic et al. 2006(Samanic et al., 2006) | ||
OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Anilides/ anilines | Acetochlor | RR 1.07 (0.66–1.73) p>0.05, IWLED RR 1.67 (0.90–3.11) p-trend 0.20 | Lerro et al. 2015(Lerro et al., 2015b) | |
Alachlor | SIR 2.56 (0.31–9.25)*^ | Acquavella et al. 2004(Acquavella et al., 2004) | ||
SIR 0.76 (0.58–0.98)*, LED RR 0.62 (0.20–1.99) p-trend 0.53, IWLED RR 1.14 (0.40–3.23) p-trend 0.64 | Lee et al. 2004b(Lee et al., 2004b) | |||
OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Metolachlor | LED RR 1.30 (0.55–3.08) p-trend 0.32 | Rusiecki et al. 2006(Rusiecki et al., 2006) | ||
OR 1.0 (0.7–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Pendimethalin | RR 0.4 (0.05–3.2)^ p-trend 0.20 | Hou et al. 2006(Hou et al., 2006) | ||
OR 1.2 (0.8–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Trifluralin | IWLED RR 1.76 (1.05–2.95) p-trend 0.036 | Kang et al. 2008(Kang et al., 2008) | ||
OR 1.0 (0.7–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Trazines | Atrazine | RR 1.26 (0.88–1.80) p-trend 0.04 | Beane Freeman et al. 2011(Beane Freeman et al., 2011) | |
LED RR 0.88 (0.41–1.89) p-trend 0.98 | Rusiecki et al. 2004(Rusiecki et al., 2004) | |||
OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Cyanizine | IWLED RR 0.57 (0.27–1.17) p-trend 0.21 | Lynch et al. 2006(Lynch et al., 2006) | ||
OR 0.8 (0.6–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Metribuzin | OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
LED 0 vs. T3 RR 2.07 (0.94–4.60) p-trend 0.06, IWLED 0 vs. T3 RR 1.69 (0.69–4.10) p trend 0.22 | Delancey et al. 2009(Delancey et al., 2009) | |||
Thiocarbamate | EPTC | LED RR 2.09 (1.26–3.47) p-trend <0.01 | van Bemmel et al. 2008(van Bemmel et al., 2008) | |
OR 1.2 (0.8–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Pyridine | Imazethapyr | RR 1.78 (1.08–2.93) p-trend 0.02, proximal colon RR 2.73 (1.42–5.25) p-trend 0.001, distal colon RR 1.21 (0.55–2.68) p-trend 0.75 | Koutros et al. 2009(Koutros et al., 2009) | |
1.2 (0.8–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Sulfonylurea | Chlorimuron ethyl | OR 0.8 (0.5–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Organophosphate | Glyphosate | LED RR 0.9 (0.4–1.7) p-trend 0.54, IWLED RR 1.4 (0.8–2.5) p-trend 0.10^ | De Roos et al. 2005(De Roos et al., 2005) | |
OR 1.0 (0.7–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Dipyridylium | Paraquat | OR 0.7 (0.5–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
RR 0.89 (0.63–1.25) * | Park et al. 2009(Park et al., 2009) | |||
Fungicides | Benimazole | Benomyl | OR 0.7 (0.4–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Phthalimide | Captan | 0 vs. T3 RR 0.90 (0.37–2.20) p-trend 0.44, T1 vs. T3 RR 0.58 (0.16–2.17) p-trend 0.23 | Greenburg et al. 2008(Greenburg et al., 2008) | |
OR 0.7 (0.4–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Organochlorine | Chlorothalonil | RR 1.46 (0.70–3.03) p-trend 0.31 | Mozzachio et al. 2008(Mozzachio et al., 2008) | |
OR 1.4 (0.9–2.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Acylalanine | Metalaxyl | OR 1.1 (0.7–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Fumigants | Other | Aluminum phosphide | OR 0.7 (0.3–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Methyl bromide | IWLED RR 0.81 (0.37–1.79) p-trend 0.77 | Barry et al. 2012(Barry et al., 2012) | ||
OR 1.3 (0.9–2.1)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Results that were statistically significant were bolded under the effect size summary.
No p-value listed in the publication.
Only one or no decimal points reported in the original publication. Lifetime exposure days (LED), Intensity weighted lifetime exposure days (IWLED), Tertile 1 (T1), Tertile 2 (T2), Tertile 3 (T3), Tertile 3 lower (T3L), Tertile 3 upper (T3U), Tertile 4 (T4)
Table 6.
Associations Between Occupational or Environmental Exposure to Pesticides and Colon Cancer, Rectal Cancer, or CRC Risk.
Group | Population | Country | Specific Population | Relative Risk summary | Reference |
---|---|---|---|---|---|
Occupational exposure | farm-related | US (Wisconsin) | farmers | PMR colon 0.96, rectum 1.13, all cohorts colon 0.87 p<0.05, rectum 1.03, 1905–1958 colon 0.89, rectum 1.27 p<0.05 PCMR high agricultural production, herbicides 1.45 p<0.05, insecticides 1.26+ | Saftlas et al. 1987(Saftlas et al., 1987) |
US (Illinois) | farmers | OR colon 1.04 p 0.54+, rectum 1.01 (0.77–1.33) p 0.94 | Keller, Howe, 1994(Keller and Howe, 1994) | ||
US (Kansas) | farmers | OR colon farmers that used herbicides for 6–15 years 2.0 (0.5–7.5)*^ | Hoar et al. 1985(Hoar et al., 1985) | ||
US (California) | farmers | PMR colon 0.98, rectum 0.92+ | Peterson, Milham, 1980(Peterson and Milham, 1980) | ||
US (Washington State) | farmers | PMR colon 0.88 p<0.05, rectum 0.94+ | Milham 1989(Milham, 1983) | ||
US (Massachusetts) | farmers | MOR colon 2.33 p<0.05+ | Dubrow, Wegman, 1984(Dubrow and Wegman, 1984) | ||
US (Iowa) | farmers | SMR colon 1.22 p<0.01, PMR 1.03+ | Burmeister 1981(Burmeister, 1981) | ||
US (North Carolina) | farmers | PMR CRC whites 0.7 (0.6–0.8), non-whites 0.7 (0.5–1.0)* | Delzell, Grufferman, 1985(Delzell and Grufferman, 1985) | ||
US (Missouri) | farmers | OR colon 0.86 (0.73–1.02), rectum 1.21 (0.95–1.53)* | Brownson et al. 1989(Brownson et al., 1989) | ||
US (South Carolina) | farmers (male) | PMR CRC white 0.61 p<0.05, non-white 0.60 p<0.05+ | Une et al. 1987(Une et al., 1987) | ||
US (California) | farm workers | OR colon 0.75 (0.53–1.05), rectum 0.85 (0.54–1.31)* | Mills, Kwong, 2001(Mills and Kwong, 2001) | ||
US (New York) |
farm bureau members | SMR colon 30–39 5.00, 40–49 0.39, 50–59 0.35 p<0.025, 60–69 0.55 p<0.025, 70+ 0.55 p<0.025, total 0.54 p<0.005+ | Stark et al. 1987(Stark et al., 1987) | ||
US (California) | California Hispanic and United Farm Workers of America | CRC Male crude HR 1.61 (1.11–2.33) p-value <0.05, age and stage in model 1.35 (0.93–1.95)*, Female HR age and stage in model 1.01 (0.45–2.24)* | Dodge, Mills, Riordan, 2007(Dodge et al., 2007) | ||
US | farmers | PCMR colon non-white men 0.78 (0.66–0.92)*, white male south 0.91 p<0.05+, non-white male south 0.81 p<0.05+ | Blair, Dosimeci, Heinman, 1993(Blair et al., 1993) | ||
US | farmers | SMR colon 0.71 p<0.05, rectum 0.79+ | Blair, Walrath, Rogot, 1985(Blair et al., 1985b) | ||
US | farmers | SMR colon 0.71 p<0.05, rectum 0.79+ | Walrath et al. 1985(Walrath et al., 1985) | ||
US | farmers | OR CRC 0.58 p<0.05+ | Decoufle et al. 1977(Decoufle and Stanislawczyk, 1977) | ||
US | farmers | SMR CRC 0.69+ | Guralnick 1963(Guralnick, 1963) | ||
US | farmers/ farm laborers | RR male colon 1.24, rectum 0.77, female colon 1.42*+ | Williams, Stegens, Goldsmith, 1977(Williams et al., 1977) | ||
US | migrant and seasonal farmworkers | PCMR colon white men 0.87 (0.75–0.99), non-white men 0.72 (0.57–0.89), white women 1.18 (0.79–1.71), non-white women 0.76 (0.55–1.03), rectum white men 0.71 (0.48–1.02), non-white men 1.04 (0.64–1.59), white women 0.60 (0.07–2.18), non-white women 0.84 (0.31–1.83)* | Colt et al. 2001(Colt et al., 2001) | ||
Italy | farmers, case-control | CRC Crude OR 3.389 (2.238–5.050) p-value <0.001, Generalized Linear Mixed Models OR 1.529 (1.011–2.314) p-value 0.044 | Salerno et al. 2016(Salerno et al., 2016) | ||
Italy | farmers | Colon OR (90% CI) 0.93 (0.60–1.43)*, Rectum 1.45 (0.82–2.59)*, rectum non-farmers vs. >10 years 4.22 (1.08–14.7) p-value <0.10 | Forastiere et al. 1993(Forastiere et al., 1993) | ||
Italy | farmers, multi-site case-control | farmers OR colon 0.8 (0.5–1.2), rectum 1.4 (0.8–2.7), production/application colon 0.8 (0.5–1.4), rectum 1.5 (0.8–2.9)*^ | Settimi et al. 2001(Settimi et al., 2001) | ||
Italy | farmers/ agricultural workers | SMR male colon 0.76 (0.31–1.58), rectum 1.06 (0.34–2.49) | Faustini et al. 1993(Faustini et al., 1993) | ||
Italy | farmers | RR CRC males 0.6 (0.3–0.9), females 1.2 (0.7–2.0), total 0.8 (0.6–1.2)*^ | Franceschi et al. 1993(Franceschi et al., 1993) | ||
Canada (Alberta) | farmers | OR CRC 1.02 (0.85–1.22)* | Fincham, Hanson, Berkel, 1991(Fincham et al., 1992) | ||
Canada (British Columbia) | farmers | PMR colon 0.84 (0.75–0.93)* | Gallagher et al. 1984(Gallagher et al., 1984) | ||
Canada | farmers, farm workers and agriculture | SMR colon farmers 0.53 p>0.05, agriculture 0.66 p>0.05+ | Howe, Lindsay, 1983(Howe and Lindsay, 1983) | ||
Canada | agricultural workers | male HR colon 0.89 (0.82–0.97), rectum 1.05 (0.95–1.16), female HR colon 0.95 (0.82–1.10), rectum 1.08 (0.88–1.32)* | Kachuri et al. 2017(Kachuri et al., 2017) | ||
Sweden | farmers | SIR colon 0.74 p<0.05, rectum 0.90+ | Statistics Sweden 1981(Sweden, 1981) | ||
Sweden | farmers (female) | SIR colon 0.90 (0.81–1.00), rectum 0.86 (0.74–1.00)* | Wiklund, Dich, 1994(Wiklund and Dich, 1994) | ||
Sweden | farmers | SIR colon 0.80 p<0.05, rectum 0.96+ | Wiklund, Einhorn, Wennstrom, 1981(Wiklund et al., 1981) | ||
Denmark and Italy | farmers | male Denmark SIR colon 0.58 p-value <0.05, rectum 0.77 p-value <0.05, Italy CRC 0.46 p-value <0.05, female Denmark colon SIR 0.21 p-value <0.05, rectum 0.38*, Italy colorectal 0.31*+ | Ronco, Costa, Lynge, 1992(Ronco et al., 1992) | ||
Denmark | farmers | colon farming adjusted OR men 0.5 (0.3–0.9), women 2.1 (0.6–7.6), both 0.7 (0.4–1.1), farming animals adjusted OR men 0.4 (0.2–0.8), women 2.0 (0.5–8.9), both 0.5 (0.3–0.9)*^ | Kaerlev et al. 2004(Kaerlev et al., 2004) | ||
Australia | farmers and farm managers (male) | CRC SMR 1.37 (0.98–1.87)* | Fragar, Depczynski, Lower, 2011(Fragar et al., 2011) | ||
Australia | farmers (male) | SRR colon 0.81 p<0.05, rectum 0.84 p<0.05+ | McMichael, Hartshorne, 1982(McMichael and Hartshorne, 1982) | ||
Iceland | farmers | SIR colon 0.47 (0.26–0.77), rectum 0.93 (0.49–1.63)* | Gunnarsdottir, Rafnsson, 1991(Gunnarsdottir and Rafnsson, 1991) | ||
Iceland | farmers | SMR colon 0.35 (0.07–1.02), rectum 1.06 (0.29–2.77)* | Rafnsson, Gunnarsdottir, 1989(Rafnsson and Gunnarsdottir, 1989) | ||
UK (England and Wales) | farmers | SMR colon 1.20, rectum 1.00+ | Fox, Goldblatt, 1980(Fox and Goldblatt, 1980) | ||
The Netherlands | farmers | PMR colon 0.78 p<0.05, rectum 0.90+ | Versluys 1949(Versluys, 1949) | ||
New Zealand | farmers | OR colon 1.10 (0.97–1.25), rectum 1.19 (1.03–1.38)* | Reif, Pearce, Fraser, 1989(Reif et al., 1989) | ||
Egypt | farmers | CRC adjusted OR pesticides 2.6 (1.1–5.9), insecticides 3.2 (1.5–6.5), herbicides 5.5 (2.4–12.3), eating from field 4.6 (1.5–14.6), working after spray 2.1 (0.7–5.9)*^ | Lo et al. 2010(Lo et al., 2010) | ||
Denmark | Agriculture, forestry, fishing | SPIR women 1.15*+ | Olsen, Jensen, 1987(Olsen and Jensen, 1987) | ||
Sweden | market gardeners/orchardists | SMR mortality intestine 0.7 (0.4–1.4), tumor morbidity intestine 0.6 (0.3–1.0), rectum 0.9 (0.5–1.5)* | Littorin et al. 1993(Littorin et al., 1993) | ||
Pesticide-related | Australia | Tick control outside workers | colon SMR 0.53 (0.20–1.16) SIR 0.52 (0.18–1.54), rectum SMR 1.62 (0.70–3.19) SIR 2.02 (0.52–7.86)* | Beard et al. 2003(Beard et al., 2003) | |
France | municipal pest-control workers | SMR colon 1.98 (0.05–11.04), rectum 5.57 (0.14–31.06)* | Ambroise et al. 2005(Ambroise et al., 2005) | ||
US (Florida) | pesticide applicators | SMR colon male 0.81 (0.59–1.10), female 1.44 (0.58–2.97), rectum male 0.78 (0.31–1.60), female 1.19 (0.02–6.63)* | Fleming et al. 1999a(Fleming et al., 1999a) | ||
US (Florida) | pesticide applicators | SIR colon male 0.70 (0.57–0.85), female 0.78 (0.37–1.44), rectum male 0.88 (0.66–1.15), female 0.56 (0.11–1.63)* | Fleming et al. 1999b(Fleming et al., 1999b) | ||
US | pesticide applicators | SMR colon private 0.7 (0.6–1.0), total 0.8 (0.7–1.0)*^ | Blair et al. 2005(Blair et al., 2005) | ||
US | pesticide applicators (male) | SMR digestive organs and peritoneum 0.84 (0.64–1.08)* | MacMahon et al. 1988(MacMahon et al., 1988) | ||
US | pesticide applicators | RR colon 0.51 (0.3–0.9)*, rectum 0.68 (0.2–2.0)*, SMR colon aerial applicators 0.55 (0.31–0.91)*, flight instructors 1.12 (0.76–1.60)*, RR flight hours colon 0.49 p-trend 0.02 | Cantor, Silberman 1999(Cantor and Silberman, 1999) | ||
US | pesticide applicators | SMR colon 1.05 (0.28–2.68), rectum 1.45 (0.02–8.07)* | Zahm 1997(Zahm, 1997) | ||
US | pesticide applicators | SIR colon 0.88 (0.76–1.01), rectum 0.81 (0.65–0.99)* | Alavanja et al. 2005(Alavanja et al., 2005) | ||
Italy | pesticide applicators | SMR colon provincial 0.74 (0.32–1.46), national 0.81 (0.35–1.59)* | Figa-Talamanca et al. 1993(Figa-Talamanca et al., 1993) | ||
Italy | pesticide applicators | SMR colon regional 0.95 (0.61–1.42), national 0.82 (0.52–1.22)* | Alberghini et al. 1991(Alberghini et al., 1991) | ||
Italy | pesticide applicators | SMR colon 0.57 (0.45–0.71)* | Torchio et al. 1994(Torchio et al., 1994) | ||
The Netherlands | pesticide applicators | SMR colon 1.03 (0.41–2.11), rectum 2.08 (0.67–4.82)* | Swaen et al. 2004(Swaen et al., 2004) | ||
The Netherlands | pesticide applicators | SMR colon 2.25 (0.69–6.54)* | Swaen et al. 1992(Swaen et al., 1992) | ||
Iceland | pesticide applicators | colon SIR 0.62 (0.12–1.81), rectal SIR total cohort 2.94 (1.07–6.40), men 3.92 (1.06–10.04), total licensed to use pesticides 4.63 (1.49–10.80)* | Zhong, Rafnsson, 1996(Zhong and Rafnsson, 1996) | ||
Sweden | pesticide applicators | SIR colon 0.81 (0.57–1.13), rectum 0.83 (0.54–1.21)* | Wiklund et al. 1989(Wiklund et al., 1989) | ||
Finland | pesticide applicators | SMR 15-year latency colon 0.95 (0.12–3.42), rectum 0.53 (0.01–2.98), SIR colon 1.31 (0.42–3.05), rectum 0.57 (0.07–2.05)* | Asp et al. 1994(Asp et al., 1994) | ||
New Zealand | pesticide manufacturers and applicators | SMR production workers colon 0.62 (0.08–2.25), rectum 2.45 (0.79–5.73), sprayers colon 1.94 (0.84–3.83), rectum 1.47 (0.40–3.76)* | t Mannetje et al. 2005(‘t Mannetje et al., 2005) | ||
UK | pesticide manufacturers and applicators | SMR colon 1.00 (0.60–1.56), rectum 0.56 (0.24–1.10)* | Coggon et al. 1986(Coggon et al., 1986) | ||
US (Alabama and Louisiana) | pesticide manufacturers | SMR other digestive system possible 1.08 (0.29–2.77), total 0.81 (0.26–1.88)* | Sathiakumar, Delzell, Cole, 1996(Sathiakumar et al., 1996) | ||
US (Michigan and Arkansas) | pesticide manufacturers (males) | SMR exposed to DDT colon 0.60 (0.01–3.32), rectum 1.56 (0.02–8.86)* | Wong et al. 1984(Wong et al., 1984) | ||
US (Colorado) | pesticide manufacturers | SMR CRC 1.15 (0.61–1.96)* | Amoateng-Adjepong et al. 1995(Amoateng-Adjepong et al., 1995) | ||
US (Louisiana) | pesticide manufacturers | SIR CRC white men 1.04 (0.21–3.04), company 1.30 (0.27–3.81), total 0.71 (0.15–2.06)* | MacLennan et al. 2002(MacLennan et al., 2002) | ||
US | pesticide manufacturers | SMR colon Plant 2 1.75, Plant 3 0.30, rectum Plant 1 1.78, Plant 3 2.42 (0.49–7.07)* | Ditraglia et al. 1981(Ditraglia et al., 1981) | ||
US | pesticide manufacturers | SMR digestive organs and peritoneum 0.86 (0.38–1.70)* | Wang, MacMahon, 1979(Wang and Macmahon, 1979) | ||
Germany | pesticide manufacturers | SIR CRC herbicide production 2.0 (0.2–7.2), maintenance 2.8 (0.1–16.0)*^ | Nasterlack et al. 2007(Nasterlack et al., 2007) | ||
Other occupations | US | chemical workers | SMR cancer of digestive organs and peritoneum 0.74 (0.43–1.21)* | Burns, Beard, Cartmill, 2001(Burns et al., 2001) | |
Denmark | factory workers | SIR colon men 1.03 (0.5–1.8), women 0.26 (0.01–1.4), rectum men 1.41 (0.8–2.4)*^ | Lynge 1998(Lynge, 1998) | ||
The Netherlands | factory workers | SMR colon factory A 2.40 (0.49–7.01), exposed 1.83 (0.38–5.35)* | Bueno de Mesquita et al. 1993(Bueno de Demesquita et al., 1993) | ||
International | workers | SMR exposed to TCDD or higher chlorinated dioxins colon 1.00 (0.75–1.31), rectum 1.32 (0.88–1.89), exposed to any phenoxy herbicide or chlorophenol colon 1.06 (0.85–1.31), rectum 1.06 (0.77–1.42)* | Kogevinas et al. 1997(Kogevinas et al., 1997) | ||
Korea | Korean Vietnam veterans | SIR colon 1.03 (0.94–1.14), rectum 0.99 (0.91–1.08), colon enlisted soldiers 0.90 (0.80–1.02), non-commisioned officers 1.24 (1.01–1.53), officers 1.52 (1.22–1.89), rectum enlisted soldiers 1.05 (0.95–1.16), non-commisioned officers 0.81 (0.64–1.03), officers 0.89 (0.69–1.16)* | Yi 2013(Yi, 2013) | ||
Korea | Korean Vietnam veterans | OR colon High exposure 2 groups 1.13 (1.01–1.26)*, High exposure 4 groups 1.05 (0.88–1.24) p-trend 0.21 | Yi et al. 2013(Yi et al., 2013) | ||
Korea | Korean Vietnam veterans | HR CRC 0.96 (0.78–1.19) p-value 0.723 | Yi et al. 2014(Yi et al., 2014) | ||
Environment al exposure | Geography-related | US | spouses of pesticide applicators | SIR colon 1.2 (0.8–1.6)* | Blair et al. 2005(Blair et al., 2005) |
US | spouses of pesticide applicators | SIR colon 0.91 (0.73–1.12), rectum 0.59 (0.38–0.89)* | Alavanja et al. 2005(Alavanja et al., 2005) | ||
UK | women in the United Kingdom | CRC RR never consumed organic food referent, usually/always 1.02 (0.93–1.12)* | Bradbury et al. 2014(Bradbury et al., 2014) | ||
England | near herbicide/ pesticide production facility | CRC PMR 1.20*+ | Wilkinson et al. 1997(Wilkinson et al., 1997) | ||
US (New York) | farm residents | SIR CRC 0.65 (0.45–0.90)* | Wang et al. 2002(Wang et al., 2002) | ||
US (New York) | farm residents | SMR CRC 0.56 (0.28–1.03)* | Wang et al. 2003(Wang et al., 2003) | ||
Australia (New South Wales) | farm residents | OR CRC men rural non-farm vs. farm 0.45 (0.19–1.07), urban vs. farm 0.49 (0.21–1.17), women rural non-farm vs. farm 1.21 (0.47–3.09), urban vs. farm 0.92 (0.36–2.35)* | Depczynski et al. 2018a(Depczynski et al., 2018b) | ||
Australia | farm residents | HR CRC men rural non-farm vs. farm 1.12 (0.86–1.46), urban vs. farm 1.02 (0.78–1.33), women rural non-farm vs. farm 1.03 (0.76–1.40), urban vs. farm 0.95 (0.70–1.29)* | Depczynski et al. 2018b(Depczynski et al., 2018a) | ||
South Korea | near farms | CRC RR men 0.82 (0.76–0.89) p-trend <0.01, women 0.87 (0.81–0.94) p-trend 0.02 | Lee et al. 2008(Lee et al., 2008) | ||
Spain | near farms | OR colon total 1.51 (1.42–1.61) p-value <0.001 | Parron et al. 2014(Parron et al., 2014) | ||
Israel | Druze Isifya Village | CRC OR 0.67 (0.12–3.78)* | Atzmon et al. 2012(Atzmon et al., 2012) | ||
Turkey | Secondary data: Antalya Cancer Registry Center | CRC women B Coefficient - 0.708, t −2.875, p-value 0.028 | Uysal et al. 2013(Uysal et al., 2013) | ||
Brazil | Secondary data | colon SMR vs. 3 of pesticides sold per Brazilian state for each year (2000–2012) used to calculate effect (beta st): roughly around 0.1–0.15 | Martin et al. 2018(Martin et al., 2018) | ||
Costa Rica | Secondary data from 81 counties | RR colon men 1.19 (0.78–1.81), women 1.65 (0.98–2.78), rectum men 1.61 (0.96–2.69) women 1.86 (1.06–3.25)* | Wesseling et al. 1999(Wesseling et al., 1999) | ||
Food-related | US (New York) | Angler Cohort Study | adjusted RR CRC ever ate 0.66 (0.35–1.24)*, years of consumption 0.51 (0.22–1.18) p-trend 0.13, colon ever ate 0.45 (0.20–1.00)*, years of consumption 0.24 (0.07–0.87) p-trend 0.02, rectal ever ate 1.25 (0.43–3.65)*, years of consumption 1.30 (0.37–4.58) p-trend 0.59 | Callahan et al. 2017(Callahan et al., 2017) | |
France | NutriNet-Sante Prospective Cohort | HR CRC cancer 0.87 (0.48–1.57) p-value 0.84 | Baudry, Assmann, Touvier, 2018(Baudry et al., 2018) |
Bolded Statistically significant.
No p-value listed in the publication.
Only one or no decimal points reported in the original publication.
No CI listed in original publication.
3.2. Studies Analyzing Certain Pesticides Exposure and Colon Cancer, Rectal Cancer, and CRC Risk
There are a few different groups of pesticides, such as OCIs and OPIs, chlorophenoxy herbicides, carbamate insecticides, anilide/ aniline herbicides, and triazine herbicides. Of the 139 studies included, 48 evaluated certain pesticides. Significant associations between certain pesticide exposure and colon cancer, rectal cancer, and CRC risk from these 48 studies are discussed below and in Figures 2 through 4 and in more detail in Tables 2 through 5. The tables and figures are sorted by cancer or analysis type (Table 2 and Figure 2 colon cancer, Table 3 and Figure 3 rectal cancer, Table 4 and Figure 4 CRC, and Table 5 serum measurement analyses). The epidemiological studies included report their results in effect sizes in which a value of greater than 1 denotes a positive association while a value of less than 1 denotes an inverse association. The biological sample measurement studies included in this review reported their results as mean abundances, levels, or concentrations and we have calculated the fold changes (not reported, cancer/control) to denote the differences between groups studied and these are reported in Table 5. Because of these differences in reporting units and values, Figures 2–4 only report the significant results of epidemiological studies with CI reported included in this review.
Figure 2. Forest Plot of the Associations (effect size: RR, HR, OR, SIR, or PMR and 95% CI) Between Certain Pesticide Exposure and Colon Cancer Risk.
The pesticides aldicarb, dicamba, fonofos, EPTC, imazethapyr, terbufos, and trifluralin show positive associations while alachlor, lindane, 2,4-D, butylate, and DDT show inverse associations between pesticide exposure and colon cancer risk. Only significant associations from epidemiological studies with CI reported have been summarized in this figure. Associations from biological sample measurement studies can be found in Table 5.
Figure 4. Forest Plot of the Associations (effect size: RR, OR, or SIR and 95% CI) Between Certain Pesticide Exposure and CRC Risk.
We have summarized that pesticides such as heptachlor, lindane, fonofos, and acetochlor have been shown to have significant positive associations, 2,4-D has been shown to have a significant inverse association, and alachlor and chlordane (one study not shown, biological sample measurement study) have been shown to have both significant positive and inverse associations with CRC risk. Only significant associations with CI reported from epidemiological studies have been summarized in this figure. Associations from biological sample measurement studies can be found in Table 5.
Table 5.
Serum Measurement-based Associations Between Pesticides and CRC Risk.
Pesticide | Pesticide level and p-value summary | Reference |
---|---|---|
DDT | mean (SD) pp-DDE CRC 230.95 (275.21) control 184.98 (205.39), pp-DDT CRC 8.49 (10.35) control 8.31 (7.17), p-values >0.05 | Abdallah, Zaky, Covaci, 2017(Abdallah et al., 2017) |
mean (SD) 2,4 DDE CRC 8.18 (4.69) control 3.95 (2.60), 4,4 DDE CRC 15.32 (8.75) control 0.68 (0.33), 2,4 DDT CRC 31.19 (6.47) control 3.47 (1.89), 4,4 DDT CRC 44.47 (9.56) control 2.13 (0.89), p-values <0.001 | Abolhassani et al. 2019(Abolhassani et al., 2019) | |
mean (SE) o,p’-DDE control 189.8 (22.6) polyp 234.1 (23.1) CRC 320.0 (34.6) p 0.01, p,p’-DDE control 174964.9 (17319.1) polyp 184837.3 (15165.3) CRC 176523.1 (15909.4) p 0.89, o,p’-DDT control 202.2 (22.4) polyp 246.7 (22.6) CRC 269.1 (27.1) p 0.19, p,p’-DDT control 7155.1 (1122.4) polyp 6662.8 (866.3) CRC 7546.8 (1077.9) p 0.82 | Lee et al. 2018(Lee et al., 2018) | |
mean (SD) DDT cancer 71 (131.9) noncancer 61.5 (51.6) rectal 48.4 (65.3) colon 92.3 (172.6) p-values >0.05 | Soliman et al. 1997(Soliman et al., 1997) | |
HCB | mean (SD) CRC 6.37 (3.85) control 6.60 (4.81), p-values >0.05 | Abdallah, Zaky, Covaci, 2017(Abdallah et al., 2017) |
gamma HCH (lindane) | mean (SD) alpha HCH CRC 11.76 (9.82) control 1.37 (0.69), beta HCH CRC 3.65 (2.26) control 0.51 (0.15), gamma HCH CRC 6.90 (7.91) control 0.37 (0.11), p-values <0.001 | Abolhassani et al. 2019(Abolhassani et al., 2019) |
mean (SE) beta HCH control 12679.1 (1562.3) polyp 18610.2 (1900.7) CRC 16696.9 (1873.3) p-value 0.05 | Lee et al. 2018(Lee et al., 2018) | |
mean (SD) beta HCH cancer 21.5 (57.4) noncancer 10.5 (13.0) rectal 16.8 (22.8) colon 26 (77.9) p-values >0.05 | Soliman et al. 1997(Soliman et al., 1997) | |
chlordane | mean (SD) oxychlordane CRC 2.10 (0.93) control 1.87 (0.89), p-values >0.05 | Abdallah, Zaky, Covaci, 2017(Abdallah et al., 2017) |
mean (SE) trans-chlordane control 90.9 (10.6) polyp 105.6 (10.2) CRC 100.1 (10.6) p 0.61, oxychlordane control 750.9 (163.2) polyp 523.4 (94.3) CRC 4079.3 (807.3) p<0.01 | Lee et al. 2018(Lee et al., 2018) | |
PCP | mean (SD) CRC 33.26 (45.87) control 28.73 (35.48), p-values >0.05 | Abdallah, Zaky, Covaci, 2017(Abdallah et al., 2017) |
nonachlor | mean (SE) trans-nonachlor control 5902.4 (747.2) polyp 6704.3 (703.4) CRC 7612.3 (877.4) p 0.39, cis-nonachlor control 556.3 (118.5) polyp 335.9 (59.3) CRC 738.2 (143.1) p 0.01 | Lee et al. 2018(Lee et al., 2018) |
heptachlor | mean (SE) heptachlor epoxide control 609.4 (112.7) polyp 719.6 (110.3) CRC 2179.2 (366.9) p <0.01, heptachlor control 188.7 (30.2) polyp 448.4 (59.5) CRC 260.6 (38.0) p <0.01 | Lee et al. 2018(Lee et al., 2018) |
Results that were statistically significant were bolded under the pesticide level and p-value summary.
No p-value listed in the publication.
Only one or no decimal points reported in the original publication. Standard deviation (SD), standard error (SE).
Table 3.
Associations Between Pesticide Exposure and Rectal Cancer Risk.
Type | Group | Pesticide | Effect size summary | Reference |
---|---|---|---|---|
Insecticides | Organochlorine | Chlordane | RR 1.80 (0.77–4.21)* | Louis et al. 2017(Louis et al., 2017) |
LED RR 2.7 (1.1–6.8) p-trend 0.03^ | Purdue et al. 2007(Purdue et al., 2007) | |||
OR 1.6 (0.97–2.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Heptachlor | OR 1.3 (0.7–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Aldrin | OR 1.4 (0.8–2.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Dieldrin | OR 1.2 (0.6–2.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Aldrin and Dieldrin | SMR 1.76 (0.21–6.34)*^ | van Amelsvoort et al. 2009(van Amelsvoort et al., 2009) | ||
SMR 3.00 (1.10–6.49) p<0.05 | Swaen et al. 2002(Swaen et al., 2002) | |||
Toxaphene | 0 vs. T3 OR 4.3 (1.2–15.8) p-trend 0.123, OR 2.1 (1.2–3.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Pentachlorophenol and Tetrachlorophenol | SMR 1.10 (0.82–1.43), SIR 1.08 (0.92–1.29)* | Demers et al. 2006(Demers et al., 2006) | ||
DDT | PMR 0.38 (0.04–1.37)*^ | Cocco et al. 1997(Cocco et al., 1997) | ||
RR 1.79 (0.76–4.22)* | Louis et al. 2017(Louis et al., 2017) | |||
OR 1.0 (0.6–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Lindane (gamma HCH) | male SIR 0.61 (0.44–0.83)* | Rafnsson 2006(Rafnsson, 2006) | ||
OR 1.1 (0.6–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Carbon tetrachloride/carbon disulfide | OR 1.1 (0.5–2.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Organophosphate | Trichlorfon | OR 1.5 (0.2–10.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Dichlorovos | OR 0.8 (0.4–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Chlorpyrifos | RR LED 0 vs. T4 3.25 (1.60–6.62) p-trend 0.035, IWLED 0 vs. T4 3.16 (1.42–7.03) p-trend 0.057 | Lee et al. 2004a(Lee et al., 2004a) | ||
0 vs. T4 OR 2.7 (1.2–6.4) p-trend 0.008, OR 1.4 (0.9–2.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Terbufos | OR 0.8 (0.5–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Fonofos | OR 1.1 (0.6–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Malathion | OR 1.0 (0.6–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Parathion | OR 0.9 (0.5–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Phorate | OR 1.0 (0.6–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Coumaphos | OR 0.9 (0.4–2.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Diazinion | OR 1.3 (0.8–2.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Carbamate | Aldicarb | OR 0.8 (0.4–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Carbofuran | OR 1.2 (0.7–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Carbaryl | OR 2.0 (1.1–3.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Butylate | OR 0.8 (0.5–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Maneb/mancozeb | OR 0.9 (0.4–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Ziram | OR 2.3 (0.7–7.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Pyrethroid | Permethrin | LED RR 0.78 (0.31–1.92) p-trend 0.29 | Rusiecki et al. 2009(Rusiecki et al., 2009) | |
crops OR 0.5 (0.2–1.3), livestock OR 1.4 (0.7–2.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Organobromine | Ethylene dibromide | OR 0.6 (0.1–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Other | Petroleum oil | OR 0.9 (0.5–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Herbicides | Chlorophenoxy | 2,4,5-TP | OR 1.3 (0.7–2.6)*^ | Lee et al. 2007b(Lee et al., 2007b) |
2,4,5-T | OR 1.1 (0.6–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
2,4-D | OR 1.1 (0.6–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
2,4-D and MCPA | white men SRR 1.32 (1.04–1.67), white women SRR 1.12 (0.81–1.57) | Schreinemachers 2000(Schreinemachers, 2000) | ||
Dicamba | OR 0.8 (0.5–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Anilides/ anilines | Acetochlor | RR 0.97 (0.48–1.95) p>0.05 | Lerro et al. 2015(Lerro et al., 2015b) | |
Alachlor | SIR 1.60 (0.19–5.80)* | Acquavella et al. 2004(Acquavella et al., 2004) | ||
SIR 0.64 (0.42–0.94)*, LED RR 0.71 (0.16–3.11) p-trend 0.77, IWLED RR 1.07 (0.23–5.07) p-trend 0.83 | Lee et al. 2004b(Lee et al., 2004b) | |||
OR 0.9 (0.5–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Metolachlor | OR 1.0 (0.6–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Pendimethalin | RR 4.3 (1.5–12.7) p-trend 0.007^ | Hou et al. 2006(Hou et al., 2006) | ||
OR 1.0 (0.6–1.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Trifluralin | LED RR 0.66 (0.22–1.99) p-trend 0.944, IWLED T1 vs. T3U RR 1.43 (0.52–3.92) p-trend 0.317 | Kang et al. 2008(Kang et al., 2008) | ||
OR 0.8 (0.5–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Trazines | Atrazine | RR 1.14 (0.66–1.96) p-trend 0.60 | Beane Freeman et al. 2011(Beane Freeman et al., 2011) | |
LED RR 1.38 (0.47–4.02) p-trend 0.65, IWLED RR 0.84 (0.29–2.44) p-trend 0.79 | Rusiecki et al. 2004(Rusiecki et al., 2004) | |||
OR 1.2 (0.7–2.0)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Cyanizine | OR 1.4 (0.8–2.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Metribuzin | OR 0.9 (0.5–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Thiocarbamate | EPTC | LED RR 1.0 (0.42–2.40) p-trend 0.91 | van Bemmel et al. 2008(van Bemmel et al., 2008) | |
OR 0.9 (0.4–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Pyridine | Imazethapyr | RR 0.77 (0.39–1.51) p-trend 0.81 | Koutros et al. 2009(Koutros et al., 2009) | |
OR 0.9 (0.5–1.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Sulfonylurea | Chlorimuron ethyl | OR 1.0 (0.6–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Organophosphate | Glyphosate | LED RR 1.1 (0.6–2.3) p-trend 0.70, IWLED RR 0.9 (0.5–1.9) p-trend 0.82^ | De Roos et al. 2005(De Roos et al., 2005) | |
OR 1.6 (0.9–2.9)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Dipyridylium | Paraquat | OR 1.5 (0.8–2.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Fungicides | Benzimazole | Benomyl | OR 1.2 (0.6–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Phthalimide | Captan | OR 1.1 (0.5–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Organochlorine | Chlorothalonil | OR 0.7 (0.3–1.7)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Acylalanine | Metalaxyl | OR 1.0 (0.5–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Fumigants | Other | Aluminum phosphide | OR 1.4 (0.6–3.5)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Methyl bromide | IWLED 1.38 (0.53–3.63) p-trend 0.48 | Barry et al. 2012(Barry et al., 2012) | ||
OR 1.1 (0.6–2.1)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Results that were statistically significant were bolded under the effect size summary.
No p-value listed in the publication.
Only one or no decimal points reported in the original publication.
Figure 3. Forest Plot of the Associations (effect sizes: RR, OR, SMR, SRR, and SIR and 95% CI) Between Certain Pesticide Exposure and Rectal Cancer Risk.
This figure shows that pesticides such as toxaphene, pendimethalin, dieldrin and aldrin, chlorpyrifos, chlordane, carbaryl, and 2,4-D and MCPA have been reported to have positive associations while alachlor and lindane has been reported to have an inverse association with rectal cancer risk. Only significant associations from epidemiological studies with CI reported have been summarized in this figure. Associations from biological sample measurement studies can be found in Table 5. *These studies analyzed the association of concurrent dieldrin and aldrin and concurrent 2,4-D and MCPA exposure on rectal cancer risk.
Table 4.
Associations Between Pesticide Exposure and CRC Risk.
Type | Group | Pesticide | Effect size summary | Reference |
---|---|---|---|---|
Insecticides | Organochlorine | Chlordane | 0 vs. T1 OR 0.5 (0.2–0.9) p-trend 0.545^, OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) |
OR polyps 1.0 (0.4–2.4) p-trend 0.94, CRC 2.3 (0.8–6.7) p-trend 0.02^ | Lee et al. 2018(Lee et al., 2018) | |||
Heptachlor | OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
OR polyps 1.8 (0.9–3.7) p-trend 0.11, CRC 6.5 (2.7–15.6) p-trend <0.01^ | Lee et al. 2018(Lee et al., 2018) | |||
Aldrin | OR 0.8 (0.6–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Dieldrin | OR 0.8 (0.5–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Toxaphene | OR 1.3 (0.96–1.9)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
DDT | p,p’-DDT OR 0.56 (0.27–1.17) p-trend 0.12, p,p’-DDE OR 1.60 (0.79–3.25) p-trend 0.19 | Howsam et al. 2004(Howsam et al., 2004) | ||
OR 0.9 (0.7–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
OR polyps 1.2 (0.5–2.9) p-trend 0.52 CRC 2.4 (0.8–6.8) p-trend 0.09^ | Lee et al. 2018(Lee et al., 2018) | |||
Lindane (gamma HCH) | Lindane (gamma HCH) OR 0.69 (0.34–1.38) p-trend 0.28, alpha HCH OR 2.02 (0.95–4.29) p-trend 0.081, beta HCH OR 0.88 (0.39–2.02) p-trend 0.81 | Howsam et al. 2004(Howsam et al., 2004) | ||
OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
ORs beta HCH polyps 6.0 (2.1–16.9) p-trend <0.01, CRC 3.7 (1.1–12.5) p-trend 0.11^ | Lee et al. 2018(Lee et al., 2018) | |||
Carbon tetrachloride/carbon disulfide | OR 0.8 (0.5–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Organophosphate | Trichlorfon | OR 1.5 (0.5–4.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Dichlorovos | OR 1.3 (0.8–1.9)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Chlorpyrifos | RR 0.95 (0.56–1.61)* | Lee et al. 2007a(Lee et al., 2007a) | ||
RR 0.87 (0.63–1.21)* | Lee et al. 2004a(Lee et al., 2004a) | |||
OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Terbufos | OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Fonofos | 0 vs. T3 OR 2.1 (1.2–3.7) p-trend 0.125^, OR 1.4 (1.0–1.9)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Malathion | RR 0.84 (0.48–1.48) p-trend 0.48 | Bonner et al. 2007(Bonner et al., 2007) | ||
OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Parathion | OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Phorate | OR 1.1 (0.8–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Coumaphos | RR 0.84 (0.37–1.89) p-trend 0.49 | Christensen et al. 2010(Christensen et al., 2010) | ||
OR 1.0 (0.6–1.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Diazinion | LED RR 1.21 (0.43–3.45) p-trend 0.61, IWLED RR 0.53 (0.13–2.23) p-trend 0.55 | Beane Freeman et al. 2005(Beane Freeman et al., 2005) | ||
OR 0.8 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Carbamate | Aldicarb | OR 1.6 (1.0–2.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Carbofuran | OR 1.0 (0.8–1.4)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Carbaryl | OR 1.1 (0.8–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Butylate | OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Maneb/mancozeb | OR 0.7 (0.5–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Ziram | OR 1.2 (0.5–2.9)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Pyrethroid | Permethrin | crop OR 0.8 (0.5–1.2), livestock OR 1.4 (0.9–2.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Organobromine | Ethylene dibromide | OR 0.6 (0.3–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Other | Petroleum oil | OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Herbicides | Chlorophenoxy | 2,4,5-TP | OR 0.8 (0.5–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) |
2,4,5-T | OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
2,4-D | OR 0.7 (0.5–0.9)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Dicamba | OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Anilides/ anilines | Acetochlor | RR 1.03 (0.69–1.53) p>0.05, RR 0.87 (0.38–1.99) p-value>0.05, LED RR 1.75 (1.08–2.83) p-value <0.05 p-trend 0.07, IWLED RR 1.59 (0.95–2.64) p-value <0.01 p-trend 0.16 | Lerro et al. 2015(Lerro et al., 2015b) | |
Alachlor | SIR 1.9 (0.4–5.6)*^ | Acquavella et al. 1996(Acquavella et al., 1996) | ||
SIR 0.72 (0.58–0.89) * | Lee et al. 2004b(Lee et al., 2004b) | |||
colon, rectum, rectosigmoid junction, and anus: SIR 3.4 (0.7–10.0), 5+ years exposure/10 year lag SIR 10.3 (2.1–30.2)*^ | Leet et al. 1996(Leet et al., 1996) | |||
OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Metolachlor | OR 1.0 (0.8–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Pendimethalin | RR 1.0 (0.3–3.4) p-trend 0.7^ | Hou et al. 2006(Hou et al., 2006) | ||
OR 1.1 (0.8–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Trifluralin | OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Trazines | Atrazine | RR 0.91 (0.67–1.23) p-value>0.05 | Lerro et al. 2015(Lerro et al., 2015b) | |
OR 0.9 (0.7–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Cyanizine | OR 1.0 (0.7–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Metribuzin | OR 0.8 (0.6–1.1)*^ | Lee et al. 2007b(Lee et al., 2007b) | ||
Thiocarbmate | EPTC | OR 1.1 (0.8–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Pyridine | Imazethapyr | OR 1.1 (0.8–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Sulfonylurea | Chlorimuron ethyl | OR 0.8 (0.6–1.2)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Organophosphate | Glyphosate | OR 1.2 (0.9–1.6)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Dipyridylium | Paraquat | OR 0.9 (0.7–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Fungicides | Benzimazole | Benomyl | OR 0.9 (0.6–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Phthalimide | Captan | 0 vs. T3 RR 0.71 (0.32–1.60) p-trend 0.10, T1 vs. T3 RR 0.51 (0.17–1.54) p-trend 0.11 | Greenburg et al. 2008(Greenburg et al., 2008) | |
OR 0.8 (0.5–1.3)*^ | Lee et al. 2007b(Lee et al., 2007b) | |||
Organochlorine | Chlorothalonil | OR 1.2 (0.8–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Hexachlorobenzene | OR 1.60 (0.62–4.15) p-trend 0.23 | Howsam et al. 2004(Howsam et al., 2004) | ||
Acylalanine | Metalaxyl | OR 1.0 (0.7–1.5)*^ | Lee et al. 2007b(Lee et al., 2007b) | |
Fumigants | Other | Aluminum phosphide | OR 0.9 (0.5–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Methyl bromide | OR 1.3 (0.9–1.8)*^ | Lee et al. 2007b(Lee et al., 2007b) |
Results that were statistically significant were bolded under the effect size summary.
No p-value listed in the publication.
Only one or no decimal points reported in the original publication.
3.2.1. Organochlorine Insecticides
Among OCIs, toxaphene (Lee et al., 2007b), aldrin and dieldrin concurrently (Swaen et al., 2002) have shown significant positive associations with rectal cancer risk, and heptachlor has shown a significant positive association with CRC risk (Lee et al., 2018). DDT showed a significant inverse association with colon cancer risk (Cocco et al., 1997) but also the metabolite of DDT, DDE, showed a significant positive association with CRC risk (Lee et al., 2018). Lindane showed significant inverse associations with both colon and rectal cancer risk (Rafnsson, 2006) but also showed a significant positive association with CRC risk (Lee et al., 2018). Chlordane showed a significant positive association with rectal cancer risk (Purdue et al., 2007) but also showed both a significant positive association (Lee et al., 2018) and a significant inverse association with CRC risk (Lee et al., 2007b). Also, nonachlor, an impurity of chlordane, has shown a significant positive association with CRC risk (Lee et al., 2018). As you can see, varying studies have found opposing results for certain pesticide exposure effects on CRC risk. These mainly positive associations (seven out of eleven) among rectal cancer and CRC risk and OCIs are understandable as DDT, lindane, chlordane, toxaphene, heptachlor, dieldrin, and aldrin are all banned or severely restricted in the US and other countries (Donley, 2019; PAN, 2020) (Table 1) based on health issues that have been shown to correlate with exposure to these pesticides. However, DDT, chlordane, and dieldrin have still been detected on imported foods as recently as 2018 (FDA, 2018) (Table 1).
3.2.2. Organophosphate Insecticides
Terbufos showed a significant positive association with colon cancer risk (Bonner et al., 2010), chlorpyrifos showed significant positive associations with rectal cancer risk (Lee et al., 2004a; Lee et al., 2007b), and fonofos showed significant positive associations with colon cancer and CRC risk (Lee et al., 2007b). These positive associations are of interest because terbufos and chlorpyrifos have no restriction in the US (Donley, 2019; PAN, 2020), have been used in the US as recently as 2017 (USGS, 2017), and chlorpyrifos is still detected on imported food products as recently as 2018 (FDA, 2018) (Table 1).
3.2.3. Carbamate Insecticides
Among carbamate insecticides, aldicarb (Lee et al., 2007b) showed a positive association and butylate showed an inverse association with colon cancer risk (Lynch et al., 2009), and carbaryl showed a positive association with rectal cancer risk (Lee et al., 2007b). These mainly positive associations are of interest because aldicarb is banned in the US (Donley, 2019; PAN, 2020) but was still being used in the US as of 2017 (USGS, 2017) and carbaryl is not banned in the US (Donley, 2019; PAN, 2020) (Table 1).
3.2.4. Chlorophenoxy Herbicides
MCPA and 2,4-D used concurrently were shown to have a significant positive association with rectal cancer risk (Schreinemachers, 2000), dicamba was shown to have a significant positive association with colon cancer risk (Samanic et al., 2006), and 2,4-D was shown to have significant inverse associations with both colon cancer and CRC risk (Lee et al., 2007b). These results are of concern because although 2,4-D and MCPA are currently banned in other countries, and 2,4-D is classified as a possible human carcinogen (WHO, 2020), they are not banned in the US and dicamba is not banned anywhere (Donley, 2019; PAN, 2020) (Table 1).
3.2.5. Anilide/ Aniline Herbicides
Of the anilide/ aniline herbicide exposures studied, significant positive associations were reported between trifluralin and colon cancer risk (Kang et al., 2008), pendimethalin and rectal cancer risk (Hou et al., 2006), and acetochlor and CRC risk (Lerro et al., 2015b). Alachlor exposure has been shown to have significant inverse associations with colon and rectal cancer risk (Lee et al., 2004b), and both a significant inverse association (Lee et al., 2004b) and a significant positive association (Leet et al., 1996) with CRC risk. These mostly positive associations are worthy of note because acetochlor and trifluralin are banned in other countries but not in the US, pendimethalin currently has unrestricted use worldwide except for Norway, and alachlor has been banned in the US (Donley, 2019; PAN, 2020) but was still being used in the US as recently as 2017 (USGS, 2017) (Table 1).
3.2.6. Other Pesticides
Of the other pesticides studied in these publications imazethapyr, a pyridine herbicide, (Koutros et al., 2009) and EPTC, a thiocarbamate herbicide, (van Bemmel et al., 2008) have been shown to have significant positive associations with colon cancer risk. These positive associations are also of public health interest because imazethapyr and EPTC are banned in other countries but not in the US (Donley, 2019; PAN, 2020) (Table 1). No significant associations were found between pyrethroid and organobromine insecticides, triazine, sulfonylurea, organophosphate, or dipyridylium herbicides, fungicides or fumigants and colon cancer, rectal cancer, or CRC risk.
3.2.7. Discussion of Pesticide Exposure and Colon Cancer Risk
In this review, seven pesticides, aldicarb (Lee et al., 2007b), dicamba (Samanic et al., 2006), fonofos (Lee et al., 2007b), EPTC (van Bemmel et al., 2008), imazethapyr (Koutros et al., 2009), terbufos (Bonner et al., 2010), and trifluralin (Kang et al., 2008) had significant medium to large positive associations with colon cancer risk (Figure 2). This is of concern because imazethapyr, terbufos, EPTC, and trifluralin are banned in other countries but not the US (Donley, 2019; PAN, 2020), aldicarb has been shown to be used in the US as recent as 2017 (USGS, 2017), and dicamba is not banned in any country (Donley, 2019; PAN, 2020) (Table 1). Also, five pesticides in this review had significant small to medium inverse associations with colon cancer risk: alachlor (Lee et al., 2004b), lindane (Rafnsson, 2006), 2,4-D (Lee et al., 2007b), butylate (Lynch et al., 2009), and DDT (Cocco et al., 1997) (Figure 2). Overall, there were more significant positive associations (7) between certain pesticides and colon cancer risk than inverse associations (5).
3.2.8. Discussion of Pesticide Exposure and Rectal Cancer Risk
Nine pesticides had significant positive associations with rectal cancer risk, including toxaphene (Lee et al., 2007b), pendimethalin (Hou et al., 2006), dieldrin and aldrin concurrently (Swaen et al., 2002), chlorpyrifos (Lee et al., 2007b), chlordane (Purdue et al., 2007), carbaryl (Lee et al., 2007b), and 2,4-D and MCPA concurrently (Schreinemachers, 2000) (Figure 3). Of these nine pesticides, seven, toxaphene, pendimethalin, dieldrin and aldrin (concurrently), chlorpyrifos, chlordane, and carbaryl, had medium or large, significant positive associations with rectal cancer risk. This is of concern because carbaryl and pendimethalin are not banned in any countries, including the US (Donley, 2019; PAN, 2020) (Table 1). Also, lindane (Rafnsson, 2006) and alachlor (Lee et al., 2004b) had small, significant inverse associations with rectal cancer risk (Figure 3). Therefore, overall more pesticides were found to be significantly positively associated (9) with rectal cancer risk than the number of those significantly inversely associated (2).
3.2.9. Discussion of Pesticide Exposure and CRC Risk
There were also studies that grouped colon and rectal cancer together into what is called colorectal cancer (CRC) and analyzed how certain pesticide exposure was associated with the risk of CRC. The pesticides and pesticide metabolites that were found to have significant positive association with CRC risk were fonofos (Lee et al., 2007b), DDT and DDE, metabolite of DDT, (Abolhassani et al., 2019; Lee et al., 2018), lindane (Abolhassani et al., 2019), heptachlor (Lee et al., 2018), and acetochlor (Lerro et al., 2015b) (epidemiological results found in Figure 4). Four of these had medium or large, significant positive associations with CRC risk: fonofos (Lee et al., 2007b), lindane (Abolhassani et al., 2019; Lee et al., 2018), heptachlor (Lee et al., 2018), and acetochlor (Lerro et al., 2015b) (Figure 4). This is of concern because acetochlor is not banned in the US (Donley, 2019; PAN, 2020) (Table 1). Also, 2,4-D was found to have a significant inverse association with CRC risk (Lee et al., 2007b) (Figure 4). In addition, chlordane (Lee et al., 2007b; Lee et al., 2018) and alachlor (Lee et al., 2004b; Leet et al., 1996) were found to have both significant positive and inverse associations with CRC risk (epidemiological study significant findings reported in Figure 4). Overall, more pesticides were found to be significantly positively associated (7) with CRC risk than the number that were found to be significantly inversely associated (3).
3.2.10. Summary of Pesticide Exposure and Colon Cancer, Rectal Cancer, and CRC Risk
From this systematic review, we found that there were 26 significant positive associations and 10 significant inverse associations reported with respect to exposure to specific pesticides and colon cancer, rectal cancer, or CRC risk. Exposure to pesticides such as aldicarb, dicamba, fonofos, EPTC, imazethapyr, terbufos, and trifluralin are positively associated with colon cancer risk (Figure 2), while toxaphene, pendimethalin, dieldrin and aldrin concurrently, chlorpyrifos, and carbaryl are positively associated with rectal cancer risk (Figure 3), and heptachlor, fonofos, and acetochlor are positively associated with CRC risk (Figure 4). This is of concern because many of these pesticides are not banned in the US (terbufos, dicamba, trifluralin, EPTC, imazethapyr, chlorpyrifos, carbaryl, pendimethalin, and acetochlor) (Donley, 2019; PAN, 2020), have been used as recently as 2017 in the US (aldicarb) (USGS, 2017), or have been detected on imported food as recently as 2018 (dieldrin) (FDA, 2018) (Table 1). We have also found that exposure to butylate has been shown to have a significant inverse association with colon cancer risk (Figure 2).
From our review, we have found conflicting results on the DDT, lindane, 2,4-D, alachlor, and chlordane exposure and CRC risk. DDT has been shown to have a significant inverse association with colon cancer risk (Cocco et al., 1997) but DDT and DDE have also been shown to have significant positive associations with CRC risk (Abolhassani et al., 2019; Lee et al., 2018). Lindane has been shown to have significant inverse associations with colon and rectal cancer risks (Rafnsson, 2006) but also has been shown to have significant positive associations with CRC risk (Abolhassani et al., 2019). 2,4-D has been found to have significant inverse associations with colon cancer and CRC risks (Lee et al., 2007b) but also significant positive associations with rectal cancer risk when used concurrently with MCPA (Schreinemachers, 2000). Alachlor was found to have significant inverse associations with colon and rectal cancer risks (Lee et al., 2004b) but also found to have both significant inverse associations (Lee et al., 2004b) and significant positive associations with CRC risk (Leet et al., 1996). Chlordane was found to have a significant positive association with rectal cancer risk (Purdue et al., 2007) but also both a significant positive association (Lee et al., 2018) and a significant inverse association with CRC risk (Lee et al., 2007b).
3.3. Studies Analyzing the Association between General Pesticide Exposure and Colon Cancer, Rectal Cancer, and CRC Risk
There were studies that focus on occupational or environmental exposure to pesticides and the association with colon cancer, rectal cancer, or CRC risk. In these studies, exposure to certain pesticides was not assessed but instead the overall pesticide exposure was analyzed. Of the 139 studies included in this review, 91 fall into this category. All comprehensive, summarized results are discussed in Table 6 and statistically significant results are discussed below and summarized in Figures 5–7 based on exposure type.
Figure 5. Forest Plot of the Associations (effect size: RR, OR, HR, SMR, PMR, SIR, PCMR and 95% CI) Between Pesticide Exposure from Farming or Agricultural Work and Colon Cancer, Rectal Cancer, or CRC Risk.
We have summarized that pesticide exposure from farming or agricultural work have been shown to have either weak or no associations with colon cancer, rectal cancer or CRC risk.
Figure 7. Forest Plot of the Associations (effect size: OR, RR, SIR, and 95% CI) Between Environmental Pesticide Exposure and Colon Cancer, Rectal Cancer, or CRC Risk.
We have summarized that environmental pesticide exposure have been shown to have either weak or no associations with colon cancer, rectal cancer or CRC risk.
3.3.1. Occupational Pesticide Exposure and the Association with Colon Cancer, Rectal Cancer, and CRC Risk
Among the at-risk populations included in this review are farmers, farm residents, pesticide applicators or manufacturing workers, Korean veterans of the Vietnam war, those exposed via food, and those exposed in the community. Various studies analyzing the association between farmer’s exposure to pesticides and colon cancer, rectal cancer, and CRC risk have found both significant positive and inverse associations (Figure 5). It has been reported that farmers in Massachusetts (Dubrow and Wegman, 1984) and Iowa (Burmeister, 1981) have shown significant positive associations with colon cancer risk. In addition, farmers in Wisconsin (Saftlas et al., 1987), Italy (Forastiere et al., 1993), and New Zealand (Reif et al., 1989) have been reported to have significant positive associations with rectal cancer risk. Also, significant positive associations with CRC risk have been found among farmers in California (Dodge et al., 2007), Italy (Salerno et al., 2016), and Egypt (Lo et al., 2010). However, studies including farmers in Canada (Gallagher et al., 1984; Kachuri et al., 2017), Sweden (Sweden, 1981; Wiklund et al., 1981), Denmark (Kaerlev et al., 2004; Ronco et al., 1992), Australia (McMichael and Hartshorne, 1982), Iceland (Gunnarsdottir and Rafnsson, 1991), The Netherlands (Versluys, 1949), Wisconsin (Saftlas et al., 1987), Washington State (Milham, 1983), New York (Stark et al., 1987), and other US populations (Blair et al., 1993; Blair et al., 1985b; Colt et al., 2001; Walrath et al., 1985) have found significant inverse associations with colon cancer risk. In addition, significant inverse associations with rectal cancer risk were reported in farmers from Denmark (Ronco et al., 1992) and Australia (McMichael and Hartshorne, 1982). Finally, farmers from Italy (Franceschi et al., 1993; Ronco et al., 1992), North Carolina (Delzell and Grufferman, 1985), South Carolina (Une et al., 1987), and another US population (Decoufle and Stanislawczyk, 1977) were found to have significant inverse associations with CRC risk. Previously, the reported inverse association among farmers and their CRC risk had been explained by their lower tobacco use and higher physical activity (Garabrant et al., 1984).
In addition to farmers, pesticide applicators are also perceived as being at increased risk of pesticide exposure, but from the studies reviewed, only one study reported a significant positive association with rectal cancer risk among Icelandic pesticide applicators (Zhong and Rafnsson, 1996). However, significant inverse associations were found between pesticide applicators in Italy (Torchio et al., 1994), Florida (Fleming et al., 1999b), and other US populations (Alavanja et al., 2005; Cantor and Silberman, 1999) and colon and rectal cancer risk. Other occupational risk factors include chemicals used at the job and chemical weapons used during wars. During the Vietnam War, Agent Orange was used, and three studies in this review looked at the association between that exposure and colon cancer risk. From this analysis, Agent Orange exposure was reported to have a significant positive association with colon cancer risk (Yi, 2013; Yi et al., 2013). These significant associations between occupational pesticide exposure and colon and rectal cancer risk are summarized in Figure 6.
Figure 6. Forest Plot of the Associations (effect size: OR, RR, SIR, SMR and 95% CI) Between Occupational Pesticide Exposure and Colon Cancer, Rectal Cancer, or CRC Risk.
We have summarized that occupational pesticide exposure has been shown to have either weak or no associations with colon cancer, rectal cancer or CRC risk.
3.3.2. Environmental Pesticide Exposure and the Association with Colon Cancer, Rectal Cancer, and CRC Risk In addition to occupational exposure, there were other populations environmentally exposed to pesticides,
including those that ate food that may have been exposed to pesticides, those who live in rural communities near farms, farm residents, and spouses of pesticide applicators. The resulting significant associations with environmental exposure and colon cancer, rectal cancer and CRC risk can be seen in Figure 7. Significant positive associations were found between people living near farms in Spain and colon cancer risk (Parron et al., 2014) as well as among populations in Costa Rica and rectal cancer risk (Wesseling et al., 1999). However, significant inverse associations have been found between food-related exposure studies in New York and colon cancer risk (Callahan et al., 2017) as well as exposure to spouses of pesticide applicators in the US and rectal cancer risk (Alavanja et al., 2005), and New York state farm residents (Wang et al., 2002) and South Korean populations living near farms (Lee et al., 2008) with CRC risk.
3.3.3. Discussion of at-risk Populations’ Pesticide Exposure and Association with Colon Cancer, Rectal Cancer, and CRC Risk
Among occupational exposure studies, there were more significant inverse associations (27) than positive associations (11) with colon cancer, rectal cancer, and CRC risk reported. Similarly, among those exposed because of their environment there were 2 significant positive associations and 4 inverse associations with colon cancer, rectal cancer, or CRC risk. Overall, there were more significant inverse associations (31) than significant positive associations (13) reported between occupational or environmental pesticide exposure and colon cancer, rectal cancer, or CRC risk. Therefore, based on the direction of these trends and the strength of their association, we conclude that environmental and occupational pesticide exposure has an inverse association with colon cancer, rectal cancer, and CRC risk.
3.4. Comparison to Past Review Articles
As a part of our literature review, we have found nine review articles related to the effect of pesticide exposure on CRC risk (Acquavella et al., 1998; Alavanja and Bonner, 2012; Alexander et al., 2012; Blair and Freeman, 2009; Blair et al., 1985a; Blair et al., 1992; Burns, 2005; Oddone et al., 2014; Weichenthal et al., 2010). We have included all of the original research articles cited in these reviews related to the effect of pesticide exposure on CRC risk except for three which we did not have full text access (Gallagher et al., 1989; Schwartz and Grady, 1986; Wiklund, 1986). Overall, previous review papers have reported that there are no associations (Alexander et al., 2012) or inverse associations between occupational or environmental exposure to pesticides and CRC risk (Acquavella et al., 1998; Blair and Freeman, 2009; Blair et al., 1985a; Oddone et al., 2014). Previous review articles that have looked at the association between certain pesticides and colon or rectal cancer risk (Alavanja and Bonner, 2012; Alexander et al., 2012; Weichenthal et al., 2010) have reported significant positive associations with exposure to eleven pesticides and colon or rectal cancer risk including aldicarb (Lee et al., 2007b), dicamba (Samanic et al., 2006), EPTC (van Bemmel et al., 2008), imazethapyr (Koutros et al., 2009), trifluralin (Kang et al., 2008), fonofos (Lee et al., 2007b), chlordane (Purdue et al., 2007), chlorpyrifos (Lee et al., 2004a; Lee et al., 2007b), pendimethalin (Hou et al., 2006), toxaphene (Lee et al., 2007b), and carbaryl (Lee et al., 2007b). These review papers also reported only one significant inverse associations between 2,4-D exposure and colon cancer risk (Lee et al., 2007b).
This review is novel and comprehensive to include all epidemiological and biological sample measurement research studies to date analyzing the association between pesticide exposure and colon cancer, rectal cancer, or CRC risk. Previous reviews have been limited on one type of pesticide or a few research articles to make their conclusions related to CRC risk. Here we identified similar amounts of reports presenting significant positive associations (39) and significant inverse associations (41) of pesticide exposure with colon cancer, rectal cancer, or CRC risk. Among the studies analyzing the association between exposure to certain pesticides and colon cancer, rectal cancer, or CRC risk we have found more significant positive associations (26) than significant inverse associations (10). Among at-risk populations in the studies that looked at general pesticide exposure, similarly to previous reviews we have reported that there were more significant inverse associations (31) between pesticide exposure and colon cancer, rectal cancer, or CRC risk found than significant positive associations (13).
3.5. Limitations of this Systematic Review
Small sample size is one of the limitations for many of the studies reviewed, resulting in a higher effect size needed to reach sufficient statistical power. Additionally, exposure misclassifications, inability to control for, or lack of information on some confounders, and lack of validity of death certificates are other common limitations of these studies. The healthy workers effect and dichotomous questions inherently place limits on the exposure level of pesticides.
The other limitation of this review is that there were 3 studies relevant to this review for which full text was unavailable, and because of this, they were not included (Gallagher et al., 1989; Schwartz and Grady, 1986; Wiklund, 1986). Additionally, some of the studies only reported the effect sizes to one or no decimal points, some did not report a CI, and some did not report p-values or p-trends, which might lead to misinterpretation depending on the extent of significance that is unknown. Another limitation of this review is that it is only a systematic, qualitative review and not a meta-analysis or quantitative review. A qualitative review and not a quantitative review was completed because of the large variation in the effect size variables used in these 139 studies.
Most of the analyses discussed in this review were epidemiological studies analyzing the association between pesticide exposure and colon cancer, rectal cancer, or CRC risk (Tables 2–4, and 6). This is important, especially when studying different communities (near farms or rural vs. urban) or occupations (such as farmers, pesticide applicators, or manufacturers). However, causal relationship cannot be established based on different endpoints (RR, HR, OR, SIR, etc.) due to the cross-sectional nature of the study. Additionally, limitations on epidemiological methods such as recall bias from self-report surveys can result in exposure misclassification in studies such as these, along with a small sample size and number of cancer cases leading to lower statistical power. Some other limitations of epidemiological studies include selection bias from loss to follow-up, self-selection bias from more educated and generally healthier populations, and the fact that most studies did not measure actual pesticide levels in biological samples.
Only a few studies (four out of 139) reviewed used biological sample measurements to study the risk of CRC from the direct measurement of pesticides and pesticide metabolites levels in human samples (Abdallah et al., 2017; Abolhassani et al., 2019; Lee et al., 2018; Soliman et al., 1997) (Table 5). These studies are commonly combined with surveys to document the history of pesticide exposure and cancer risk confounders and therefore improve the accuracy and predictive power. However, the biological sample measurement studies reviewed all analyzed serum samples, and none have used stool, colon wash, colon tissue, or polyps, which are more relevant to the target sample to answer research questions on colon or rectal cancer. In addition, blood exposure studies are limited by analytical technique (gas chromatography, liquid chromatography, liquid chromatography-mass spectrometry, gas chromatography-mass spectrometry, or enzyme-linked immunosorbent assay) and the analytical technique used may affect the limit of detection, sensitivity, and accuracy. Therefore, the measurement of pesticides and their metabolites in these other types of biological samples, such as stool, would reflect the actual environment within those organ sites. Fecal samples that contain pesticides, metabolites, and microbes have gained more interest in the past decade and can be collected in a non-invasive way. Ultimately, biological sample measurement studies could be used to identify the time since last exposure based on half-lives of certain pesticides and to determine levels of unauthorized use of pesticides to understand the length of time these pesticides may linger in the human body.
4. Conclusions
As previously mentioned this is a systematic, qualitative review and not a quantitative, meta-analysis. Therefore, we have not used the reported results from these reviewed studies to calculate an overall quantitative conclusion. Based on this review, a general conclusion cannot be drawn from the associations between pesticide exposure and colon cancer, rectal cancer, or CRC risk due to similar numbers of significant positive (39) and inverse (41) associations reported. We were however able to determine which particular pesticides should be of higher concern and should be studied further with respect to colon cancer, rectal cancer, or CRC risk.
From this literature review, we ranked the pesticides into three groups based on the concern in regards to these types of cancers (low, moderate, and high concern). These rankings are based on the reported associations between pesticide exposure and risk of these types of cancers as well as their recent use in the US, whether they were detected on imported food to the US, and whether they are banned in the US. The pesticides that showed no significant association or only inverse association with colon cancer, rectal cancer, or CRC risk are of low concern. The pesticides that showed a significant positive association with colon cancer, rectal cancer, or CRC risk but have been banned in the US and other countries (fonofos, aldrin, toxaphene, and heptachlor) (Donley, 2019; PAN, 2020) (Table 1) are also of low concern. However, aldicarb and dieldrin, which showed significant positive association with CRC risk and have been banned in the US and other countries, are of moderate concern because dieldrin residues were detected on food products imported into the US as of 2018 (FDA, 2018) and aldicarb has been shown to be used in the US as recently as 2017 (USGS, 2017) (Table 1). The pesticides that have been reported to have both positive and inverse associations with colon cancer, rectal cancer, or CRC risk should be studied further and therefore are of moderate concern (DDT, lindane, 2,4-D, alachlor, chlordane). MCPA, which has been shown to have small positive associations with rectal cancer (when used concurrently with 2,4-D) and has not been banned in the US (Donley, 2019; PAN, 2020) (Table 1), is also of moderate concern. Terbufos, dicamba, trifluralin, EPTC, imazethapyr, chlorpyrifos, carbaryl, pendimethalin, and acetochlor are of high concern because not only have they been shown to have significant positive associations with colon cancer, rectal cancer, or CRC risk, but they also have not been banned in the US (Donley, 2019; PAN, 2020) (Table 1). Based on these results we believe that the pesticides of moderate and high concern should be studied further among larger and more diverse populations in order to provide more supporting evidence of their concern. If these pesticides are found to be positively associated with these types of cancer in these more diversely populated future studies then they should be evaluated and banned in the US as well.
When it comes to the type of pesticides, there does not seem to be any clear trends with respect to concern over colon cancer, rectal cancer, or CRC risk. The majority of OCIs studied have been banned because of their health concerns, and triazine pesticides have not been shown to have any significant associations. In the other pesticide groups studied (OPIs, carbamates, chlorophenoxy, anilides/ anilines, and other pesticides) there are pesticides of moderate to high concern in all groups studied.
Overall, this review demonstrates that certain pesticides are positively associated with colon cancer, rectal cancer, or CRC risk and that certain pesticides are of high concern in relation to these types of cancers. More epidemiological and biological sample measurement-based research is needed, especially analyzing the association between the exposure of pesticides that are not banned in the US or anywhere and their association with CRC risk. These future studies would provide more evidence to support potentially banning or restricting these pesticides in the future if they are found to be positively associated with CRC among a larger, more diverse population or in different regions or to inform at-risk communities about these associations. The association of pesticide exposure on the risk of these types of cancers should be studied on various populations such as urban residents, rural residents potentially living near farms, and those who may be exposed to these pesticides at their job (farmer, pesticide applicator, and manufacturing). These studies would show the differences in the effect size and 95% CI which would suggest the difference in the exposure and cancer risk.
More importantly, more biological sample measurement studies are needed to determine the amount of time the pesticides or their metabolites remain in the environment (plants, produce, soil, dust, and water) or bio specimen from the population (blood, urine, saliva, and stool). If they remain in the environment or body for a longer time than anticipated, they may be able to cause more harm, especially with regards to long-term diseases such as CRC and they may be able to still cause harm even though they have been banned. These biological sample measurement studies should also examine whether these pesticides or their metabolites can be detected in more appropriate sample types such as stool or colon wash for colon cancer, rectal cancer, and CRC risk-based studies. Metabolites in the stool could be directly related to colorectal health. Participants with a recent colonoscopy could be impactful to this type of research because the status of their current colorectal health would be known.
Highlights.
Health disparity among rural communities in relation to colorectal cancer
Colorectal cancer is associated with lifestyle, environment, and occupation
Systematic review on pesticide exposure effect on colorectal cancer risk
Specific pesticide exposures positively associated with colorectal cancer risk
Acknowledgements
We thank Richard Beger (Chief, Biomarkers and Alternative Models Branch, Division of Systems Biology, National Center for Toxicological Research) for his advice and insight into metabolomics and biological sample measurements. The project described was supported by the Arkansas Center for Health Disparities grant 5U54MD002329 through the National Institute of Minority Health and Health Disparities (NIMHD), National Institutes of Health (NIH). The content is the sole responsibility of the authors and does not necessarily represent the official views of the NIH.
Funding Support
The project described was supported by the Arkansas Center for Health Disparities (5U54MD002329) through the National Institute of Minority Health and Health Disparities, National Institutes of Health (NIH), and the University of Arkansas for Medical Sciences Center for Biomedical Research Excellence Host Response to Cancer Therapy studies (P20GM109005) funded by the National Institute of General Medical Sciences. The content is the sole responsibility of the authors and does not necessarily represent the official views of the NIH.
Abbreviations:
- CRC
colorectal cancer
- US
United States
- MCPA
2-methyl-4-chlorophenoxyacetic acid
- DDT
dichlorodiphenyltrichloroethane
- DDE
dichlorodiphenyldichloroethylene
- HCB
hexachlorobenzene
- 2,4,5-TP
2-(2,4,5-trichloropehnoxy) propionic acid
- EPTC
S-ethyl dipropylthiocarbamate
- 2,4-D
2,4-dichlorophenoxyacetic acid
- PCP
pentachlorophenol
- TCP
tetrachlorophenol
- PRISMA
Preferred Reporting Items for Systematic Reviews and Meta-Analyses
- OR
Odds ratio
- RR
relative risk/risk ratio
- HR
hazard ratio
- SIR
standardized incidence ratio
- SMR
standardized mortality ratio
- SRR
standardized risk ratio
- PMR
proportionate mortality ratio
- PCMR
proportionate cancer mortality ratio
- MOR
mortality odds ratio
- CI
confidence interval
portable document format
- OCI
organochlorine insecticides
- OPI
organophosphate insecticide
- LED
Lifetime exposure days
- IWLED
Intensity weighted lifetime exposure days
- T1
Tertile 1
- T2
Tertile 2
- T3
Tertile 3
- T3L
Tertile 3 lower
- T3U
Tertile 3 upper
- T4
Tertile 4
- SD
standard deviation
- SE
standard error
- NIMHD
National Institute of Minority Health and Health Disparities
- NIH
National Institutes of Health
Footnotes
Publisher's Disclaimer: This is a PDF file of an unedited manuscript that has been accepted for publication. As a service to our customers we are providing this early version of the manuscript. The manuscript will undergo copyediting, typesetting, and review of the resulting proof before it is published in its final form. Please note that during the production process errors may be discovered which could affect the content, and all legal disclaimers that apply to the journal pertain.
CRediT Authorship Contribution Statement
Eryn K. Matich: Conceptualization, Methodology, Validation, Investigation, Data Curation, Visualization, Writing – original draft, Funding acquisition; Shelbie Stahr: Visualization for Figures 2–7, Revisions; Ping-Ching Hsu and L. Joseph Su: Conceptualization, Advising, Supervisions, Revisions; all authors: Writing – review & editing.
Declaration of Competing Interest
The authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper.
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