Even stratification into more sensitive subgroups did not yield any significant findings

Further evidence of plausibility comes from the finding that PM associated adverse health effects cover a continuous spectrum of severity . In addition to increased mortality, this spectrum includes increased hospitalizations for cardiovascular and respiratory diseases , emergency department and other health care visits for asthma and other respiratory symptoms , prevalence of atherosclerosis , decreased lung function and lung function growth , and increased respiratory infections and respiratory symptoms .In addition to cross-sectional and prospective cohort studies, panel studies have become an important tool for assessing the effects of particulate pollution on respiratory and other health outcomes. Such studies use repeated measurements of the outcome of interest in a fairly small group of subjects and correlate them with daily changes in ambient concentrations of PM and other air pollutants, which are generally obtained from central monitoring sites. A significant association between particulate pollution and declines in PEFRs as well as increased prevalence of cough and lower respiratory symptoms has been reported in some panels of unselected children but not in others . In other studies, only children with asthma or asthmatic symptoms appeared to be susceptible to the effects of particulate air pollution . Similarly, in panels of unselected adults, associations of PM and other air pollutants with increases in the prevalence of decrements in PEFR greater than 20 or in respiratory symptoms were only observed in those with chronic respiratory symptoms or increased airway lability but not in those without . Such findings suggest that patients with obstructive airway disease are more susceptible to the adverse effects of particulate air pollution. Therefore,vertical farming units most panel studies have focused on children and adults with asthma or, more rarely, COPD. Significant negative associations between daily fluctuations in PM10 and PEF deviation or prevalence of PEF decrements greater than 10 and 20% have been reported in asthmatic children . An association of borderline significance was also noted in one panel of patients with COPD .

These are not entirely consistent findings . Notably, no effect of PM10 on PEFR were observed in the Pollution Effects on Asthmatic Children in Europe study, one of the largest panel studies on air pollution and respiratory health in children with chronic respiratory symptoms, involving more than 2000 children in 14 European centers .The association between exposure to PM10 and other lung function measures, such as FEV1 or FVC, has been investigated more rarely. Significant negative associations between residential outdoor and, to a lesser extent, central site PM10 values and FEV1 were observed in children with asthma from southern California . In a panel of 86 children with asthma from Detroit, PM10 and 8-h peak O3 levels with a 2-d lag showed a significant negative correlation with diurnal variability in FEV1 and lowest daily FEV1 value . However, others were unable to detect an effect of PM10 on FEV1 or FVC . In numerous panel studies of children and adults with asthma, a significant association has been detected between elevations in PM10 concentrations and increased incidence and prevalence of cough, phlegm, specific respiratory symptoms, or symptom scores . Similar associations have been reported in patients with COPD . Again, there have been studies that have not confirmed these findings, including the large PEACE study . Some panel studies with asthmatic children and adults have indicated that the prevalence of asthma medication use rises during, or shortly after, periods of elevated PM pollution . Associations have been reported between both bronchodilator and maintenance medication use and various PM size fractions, including PM10 and PM2.5 as well as UFPs. However, others failed to observe a significant effect of PM on the prevalence of asthma medication intake or the daily dose . Several studies have analyzed potential interactions between the effects of anti-inflammatory medication use and exposure to ambient PM on asthma symptoms and lung function .

In some investigations, associations between PM and increased symptoms and/or decreased lung function were only noted, or were stronger, in those subjects who were taking anti-inflammatory medication . This was even reported from panels whose prevalence of asthma medication use increased in association with elevated particulate pollution . Note that this increased overall medication use did not necessarily affect the associations of PM with lung function in the same way it influenced the association with symptoms . Others were unable to detect a significant interaction between the effects of anti-inflammatory medication use at baseline and PM10 exposure on asthma symptoms or lung function . Finally, there have also been studies in which particulate air pollution significantly affected lung function, exhaled NO , or symptoms to a much greater extent, or exclusively in children who did not take inhaled corticosteroids. Some of these discrepancies may have resulted from the fact that some studies assessed medication use only at baseline, whereas others assessed medication use during the entire follow-up period. Additionally, the effects of particulate pollution on lung function and symptoms were observed at different lag and averaging times in the various studies. The averaging time for particulate concentrations, symptom severity of the subjects, and medication use were all found to have a major impact on the association between PM pollution and increased symptom scores in a study of 25 children and adolescents with asthma in southern California . The largest effect of 24-h mean PM10 concentrations was noted in less symptomatic children who did not take anti-inflammatory medications, whereas more symptomatic asthmatics showed the greatest increase in symptoms in association with short-term PM10 excursion . No association between PM10 at any averaging or lag time could be detected in subjects who took anti-inflammatory medications, whereas non-medicated subjects exhibited large and significant increases in symptom scores in association with same day 8-h maximum and 24-h mean PM10 levels as well as with their 5-d moving averages. Overall, the available data suggest that anti-inflammatory medication and possibly bronchodilator use provide some protection from the effects of particulate pollution on lung function and symptoms in patients with asthma.

Protection may be incomplete if the type or dose of medication is inadequate. In some patient groups, however, medication use appears to be a marker of asthma severity, which confounds the protective effects of anti-inflammatory therapy. Interactions have been observed not only with medication use but also with respiratory infections. In a panel of 86 children with asthma living in Detroit, both PM2.5 and PM10 were significantly associated with decreased lung function in children with upper respiratory infections with a 3- to 5-d lag, whereas PM2.5 did not show significant effects in the absence of upper respiratory infections . Others did not detect a significant interaction between the effects of respiratory infections and concentrations of particulate air pollution on percent predicted FEV1 . When symptom severity was the outcome of interest, however, the same investigators found significantly stronger associations with various averaging times of PM10, O3 , and NO2 during respiratory infections, with some of the ORs increasing up to fivefold .Numerous panel and some cross-sectional population-based studies have investigated the association of PM10 and PM2.5 with time- and frequency-domain parameters of heart rate variability . In panel studies, small, but significant, decreases in time domains, such as the standard deviation of all normal-to normal intervals and the square root of the mean of the sum of the squares of differences between adjacent NN intervals were observed in association with daily fluctuations in centrally monitored PM2.5 and PM10 concentrations as well as in association with personal exposure to UFPs . Frequency domains of HRV,weed drying room such as high- and low-frequency power, also showed small but significant inverse associations with daily changes in outdoor and indoor PM2.5 concentrations or the time-weighted total exposure derived from them . They also decreased significantly in association with fluctuation in personal exposure to sub-micrometer particles . The inability to detect significant effects of PM2.5 and PM10 on HRV in some other panel studies likely results from the small sample sizes, low absolute pollution levels in both of the locations, low variability of PM2.5 measurements for most subjects, and, possibly, differences in the composition of particles from these cities compared with other metropolitan areas. Most of these panel studies were conducted in elderly subjects, and there are indications that the elderly are more susceptible to the effects of particulate pollution on HRV than younger adults . Susceptibility appears to be further enhanced in subjects with underlying cardiovascular disease and hypertension , although others did not observe a significant effect modification by CVD . However, some effects on HRV have also been reported in young subjects in association with personal PM2.5 and UFP exposure , with the effects of UFPs being smaller in young subjects than in older subjects studied simultaneously . Additionally, brief occupational and environmental exposures to PM2.5 were significantly associated with decreased SDNN in relatively young cohorts of boilermakers . In striking contrast to the fairly consistent finding of decreased HRV, in nine North Carolina State Highway Patrol troopers, PM2.5 exposure inside their vehicles was associated with increased HRV and other changes suggestive of increased vagal tone . Principal factor analysis of components of PM2.5 and associated pollutants indicated that these changes were associated most strongly with PM resulting from brake wear and engine emissions .

This type of PM may exert different effects than ambient particles from other sources. The results of controlled exposure studies are also not entirely consistent with these findings . Note that particle concentrators used to generate CAPS concentrate fine particles but not UFPs. This could account for some of the differences between the results of controlled exposure studies with CAPS compared with those of panel studies because UFPs were shown to exert significant effects on HRV . Overall, however, there is rather consistent evidence that exposure to PM results in changes in cardiac autonomic control, and the decreases in SDNN in r-MSSD suggest reduced parasympathetic tone. Exposure to particulate air pollution is also associated with a decrease in heart rate , which is consistent with an increase in sympathetic tone; however, an association has not been evident in all studies .Specific rotation factor analysis of the elemental composition of fine and course PM measured in six US cities indicated that PM2.5 from mobile sources showed the strongest association with overall daily mortality, followed by particles from coal combustion sources . Fine particles from crustal sources were not associated with mortality. Interestingly, a 10-µg/m3 increase in particles from mobile sources was associated with a 2% increase in deaths from ischemic heart disease, but this was not statistically significant. An adverse effect of traffic-related particles on respiratory deaths was not evident. Conversely, deaths from COPD and pneumonia increased with increased exposure to particles from coal combustion sources, whereas this factor did not affect deaths from ischemic heart disease. Similarly, analysis of data from 14 US cities regarding PM10 emissions by source category indicated that hospital admissions for CVD were most strongly correlated with increasing percentage of PM10 from highway vehicles and highway diesels . A correlation between percentage of PM10 from highway vehicles/ diesels and hospitalization for COPD was not observed for the entire data set but became significant after exclusion of two cities . These findings are consistent with reports of increased mortality and morbidity in association with indicators of traffic and traffic-related air pollution, such as black smoke and NO2 . Additionally, in several studies, , including some analyses of the effects of air pollution on respiratory health , some investigators found black smoke to be more strongly associated with adverse health effects compared with PM10 or PM2.5 . EC and organic carbon are also likely to be derived largely from traffic emissions. In Hispanic children living in an area of Los Angeles with high traffic density, an asthma symptom score was more strongly associated with EC and OC than with PM10 . In two-pollutant models that included EC and OC along with PM10, the OR for PM10 was reduced to 1.0, whereas the ORs of EC and OC remained unchanged. The composition of PM does not vary only by emission source; even ambient particles used for CAPS studies show considerable day to-day variation in their OC, EC, and elemental composition .

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Sea mammals are predators at the top of their food chains and contain very high levels of OCs

Total, dimethyl, and diethyl DAP in urine were all significantly associated with an increased number of abnormal reflexes and the proportion of neonates with more than three abnormal reflexes . Interestingly, the association differed depending on the age at which the Brazelton Neonatal Behavioral Assessment Scale was administered. The association was negative in neonates examined after age 3 d but was unexpectedly positive in infants assessed within the first 3 d of life . An ecological study of 4- to 5-yr-old Yaqui children in Mexico demonstrated decreases in stamina, hand–eye coordination, and recall and an almost complete inability to draw a person in children living in an agricultural valley who were exposed to multiple pesticides compared to children from families living in the foothills who were employed in ranching . Notably, the two groups shared genetic, cultural, and social traits and differed mostly in type of parental employment and the use of pesticides and chemical fertilizers. Several other cohorts have been established for the investigation of the effects of in utero OP pesticide exposure on pregnancy and neurodevelopmental outcomes. Only pregnancy outcomes have been reported for these cohorts as well as for women of the CHAMACOS project. In the CHAMACOS cohort, DAP metabolites were associated with a significant increase in head circumference and a marginally significant increase in birth length . Only dimethyl phosphate, and not DEP, metabolites and cord cholinesterase activity were significantly associated with decreased length of gestational duration. In marked contrast, in a cohort of African-American and Dominican women from New York, cord blood concentrations of chlorpyrifos were a significant independent predictor of decreased birth weight and birth length . Ethnic-specific regressions indicated that the effect on birth weight was statistically significant only among African-American women, whereas the effect on birth length was significant only in Dominican women. An extension of this study confirmed the significant association between cord plasma chlorpyrifos and diazinon levels and decreased birth weight and length in a somewhat larger cohort,vertical growing systems but it was unable to detect an association with insecticide concentrations in maternal personal air during pregnancy.

Notably, although the associations between cord plasma concentrations of chlorpyrifos and diazinon were highly significant in children born before the US EPA started to phase out residential use of these pesticides, they were no longer detected in children born after. However, only cord plasma chlorpyrifos, but not diazinon, levels were significantly decreased in the relevant period. In a different cohort of pregnant women in New York, no association was detected between self-reported pesticide use during pregnancy, urinary levels of TCPy, or pyrethroid metabolites obtained during the third trimester and birth weight, length, head circumference, or gestational age . However, when maternal activity of the phase-II detoxifying enzyme paraoxonase 1 activity was accounted for, maternal urinary chlorpyrifos metabolite levels were associated with a small, but significant, decrease in head circumference. Most of the enzymes involved in the metabolism, activation, and detoxification of OP pesticides and other chemicals discussed here exhibit polymorphisms that greatly influence enzyme activity. This study represents one of the rare examples where at least one of these polymorphisms was accounted for. Notably, urinary levels of pesticide metabolites are highly variable, and measurements obtained at three different time-points show significant within-person variability . Therefore, one or two spot-urine samples are unlikely to provide a reliable measure of pesticide exposure throughout pregnancy. This may partially explain the inconsistent findings regarding birth outcomes in the aforementioned studies. Whether cord plasma or meconium concentrations constitute a more reliable measure remains to be established.Chronic exposure of rats to the pesticide rotenone has been found to constitute an animal model of Parkinson’s disease that reproduces the typical biochemical, molecular, anatomical, and behavioral findings in Parkinson’s disease . These include binding to complex I in the brain, selective nigrostriatal dopaminergic degeneration with relative sparing of the dopaminergic fibers in medial aspects of striatum, cytoplasmic inclusions containing ubiquitin and α-synuclein resembling the Lewy bodies associated with Parkinson’s disease, and hypokinesia and rigidity.

Notably, rotenone is a “natural” plant-derived compound that even organic farmers use on vegetable crops. Several epidemiological studies have suggested an association between agricultural work, which usually includes pesticide exposure, or pesticide exposure per se and idiopathic Parkinson’s disease , although others have found only suggestive evidence for such an association or have found no association . There is increasing evidence that occupational exposure to certain pesticides increases the risk of several cancers, including cancers of the brain and lungs , acute myeloid leukemia , and possibly multiple myeloma . Children may be particularly sensitive to the carcinogenic effects of pesticides, as suggested by numerous reports of associations between residential pesticide exposure and childhood cancers—particularly brain cancer and leukemia but also Wilm’s tumor, Ewing’s sarcoma, and germ cell tumors . Because cholinergic nerves in the vagi provide the major neural control of airway tone and reactivity, it seems plausible that OPs could induce airway hyperreactivity and asthma . Seven days after a single subcutaneous injection of 70 mg/kg of chlorpyrifos, vagally induced bronchoconstriction was found to be potentiated in guinea pigs in the absence of AChE inhibition . This effect was accompanied by decreased M2 muscarinic receptor function, whereas M3 receptor function was not affected. Similar results were obtained 24 h after administration of 1 or 10 mg/kg of parathion and 0.75 or 75 mg/kg of diazinon, although only the higher doses inhibited AChE . Intraperitoneal administration of parathion to guinea pigs increased lung resistance and mucus secretion and induced pulmonary edema . These broncho-obstructive effects were demonstrated to depend on the biotransformation of parathion by P450 enzymes. Even doses that did not increase lung resistance were able to induce airway hyper responsiveness not only to ACh but also to histamine. The latter was prevented by atropine, suggesting the involvement of a cholinergic mechanism. In the Agricultural Health Study, data collected on more than 20,000 farmers indicated that use of the OPs malathion and chlorpyrifos dose-dependently increased the risk of wheeze, and parathion also carried an elevated OR . It remains to be established whether OP pesticides at environmental exposure levels increase the risk of asthma and asthma-like symptoms.

OCs comprise a diverse group of synthetic chemicals that include not only pesticides but polychlorinated biphenyls , polybrominated biphenyls, polychlorinated dibenzofurans , and polychlorinated dibenzodioxins . OC pesticides include 1,1,1-trichloro- 2,2-bisethane ; lindane and other hexachlorocyclohexanes; cyclodienes such as dieldrin, chlordane, and heptachlor; and hexachlorobenzene. Many OCs—particularly the more heavily chlorinated ones—resist biotic and abiotic degradation and are lipophilic; therefore, they not only bio-accumulate in all parts of the environment,curing marijuana but are bio-concentrated from one trophic level to the next. PCDDs and PCDFs are tricyclic aromatic compounds. Because they can be substituted with between one and eight chlorine atoms, there are potentially 75 different PCDD and 135 PCDF congeners . However, the actual number present in biotic samples is much lower, and mainly 2,3,7,8-substituted congeners are detected. The most toxic congener is 2,3,7,8-tetrachlorodibenzo-p-dioxin , often referred to simply as “dioxin,” whereas the PCDDs are called dioxins. There are 209 possible PCB congeners, which differ in the degree of chlorination and the position of the chlorine atom; however, depending on the species and its trophic level, only between 50 and 150 congeners are detectable in biotic samples . Whereas PCDDs and PCDFs have rigid planar structures, the two rings of PCB molecules are joined by a single carbon–carbon bond, thus allowing axial rotation of the benzene rings. This freedom is restricted by the number and positions of the chlorine substituents and decreases from nonortho via mono-ortho to di-, tri-, and tetraortho PCBs. Planar PCBs exhibit the greatest resemblance to the dioxins. Whereas PCBs and polybrominated biphenyls were purposely produced for use as dielectric fluid in transformers and capacitors, hydraulic fluid, plasticizers, and fire retardants, PCDD/Fs arise as byproducts of thermal and industrial processes, particularly via incineration of municipal and hazardous waste. PCBs were produced in the United States from the 1920s until they were banned in 1977, with peak production occurring during the 1960s and 1970s. Historical global production of PCBs is conservatively estimated at 1.3 million tons, which were used almost exclusively in the Northern hemisphere . Emissions of PCBs were estimated to be in the range of 440 and 92,000 tons , and other data strongly have suggested that actual emissions were closer to the upper estimate . The environmental residence times of two of the major PCB congeners, PCBs 153 and 180, were recently estimated to be 110 and 70 yr, respectively ,suggesting that although the production of PCBs was halted approx 30 yr ago, exposure will continue for decades, if not centuries.Because persistent OCs are lipophilic, resist metabolism and bio-degradation, and bio-accumulate to similar extents in various biota, humans are simultaneously exposed to complex mixtures of these compounds. However, the precise nature of the mixture depends on various factors such as solubility, volatility, and rates of degradation as well as dietary and other lifestyle factors and geographic location. For the purposes of risk assessment and regulatory action, the concept of toxic equivalency factors has been developed . It is based on evidence that PCDDs, PCDFs, and certain PCBs exert their toxicity via binding to the aryl hydrocarbon receptor and subsequent induction of gene expression, particularly of various cytochrome P450 isozymes. The TEF concept assumes that the combined effects of these OCs can be predicted by a model of concentration addition. TEF values can then be used to calculate toxic equivalent concentrations by multiplying the concentrations of each PCDD, PCDF, or PCB by its TEF. Commonly, either the World Health Organization TEQs or the international TEQs developed by the NATO are used.

Inhalation of airborne OCs, stemming mostly from municipal and industrial incinerators and open burning of household trash, and dermal exposure make comparatively minor contributions to exposure. More than 90% of current exposure to background levels of PCBs and DDT and its metabolite dichlorophenyl dichloroethylene is believed to come from the dietary intake of contaminated foods—particularly dairy products, meat, and fish . Fish can contribute 75% or more of total PCDD/F and PCB TEQ ingestion in countries with high fish consumption , and in several studies, intake of fish—particularly from highly contaminated waters like the Great Lakes or the Baltic sea— has shown a significant association with serum concentrations of PCBs and their metabolites and PCDD/Fs . Notably, the traditional diet of many Arctic populations includes substantial amounts of marine foods, including sea mammals. Although OCs have been produced and used primarily in the lower and middle latitudes of the Northern hemisphere, long-range transport via the predominantly northward flow of rivers and ocean and atmospheric currents results in high exposure levels in the Arctic . Because of their lipophilicity and resistance to bio-degradation, many OCs bio-accumulate in fatty tissues and are bio-magnified in the aquatic food webs. Their consumption is associated with concentrations of PCBs and other OCs in serum, breast milk, and adipose tissue samples obtained from various Inuit populations that are up to fivefold higher than in other North American or European populations . In the United States, daily dietary intake of dioxin TEQs in the early 1990s was estimated to be 0.3 to 3.0 pg/kg body weight TEQs for an adult who weighed 65 kg . Estimates in eight European countries during the 1990s varied between 65 pg I-TEQ/d in the Netherlands and 210 pg I-TEQ/d in Spain, which is equivalent to 1 to 3 pg I-TEQ/kg body weight/d assuming a body weight of 70 kg . A more recent market basket study conducted in Finland on almost 4000 samples representing 228 food items, combined with results of a 1997 dietary survey, produced a similar estimate of 115 pg WHOTEQ/d, or 1.5 pg WHO-TEQ/kg body weight using an average weight of 76 kg . Up to threefold higher values for mean daily PCB and dioxin intake estimates have been reported for children . In most of the countries,the contributions of dioxins and dioxin-like PCBs to total TEQs were roughly equal, varying between approx 40 and 60%. Together, these data indicate that the daily intake of dioxin TEQs of many Europeans exceeded and probably still exceeds the TDI of 1 to 4 pg/kg/d recommended by the WHO .

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Formaldehyde is well-established as an irritant of the eye and upper respiratory tract

A much smaller study also indicated that many VOCs are present at higher levels in homes than in offices . In the absence of exposure to environmental tobacco smoke , the geometric mean time-weighted micro-environment concentrations of many VOCs closely approximated measured personal concentrations of these compounds in subjects from Helsinki . Acceptable lifetime cancer risk benchmarks have been established for various VOCs. In a recent study that monitored VOC exposure of 25 adults in three districts in Minneapolis/St. Paul, only the 90th percentile of outdoor concentrations of benzene and carbon tetrachloride exceeded such benchmark concentrations . Conversely, even the median personal and residential indoor concentrations of benzene exceeded the benchmark, and the 90th percentile indoor and personal exposure levels were higher than the risk threshold for three of the other five VOCs for which benchmarks are available. Similarly, in the SHIELDS study of children from two inner-city schools in Minneapolis, researchers found that median indoor residential and personal exposure levels of p-dichlorobenzene and benzene were above the acceptable risk thresholds during at least one of the seasons of measurement . Other hazardous air pollutants listed in the Clean Air Act Amendment, such as styrene, benzaldehyde, phenol, 2-butoxyethanol, and hexanal,indoor cannabis grow system are mucous membrane irritants, although at far greater concentrations than are generally encountered in indoor environments. 2-Butoxyethanol and oxidation products of Dlimonene are skin-contact allergens .It was recently reported that formaldehyde at a concentration of 0.1 µg/mL increased the expression of intracellular adhesion molecule – 1 and vascular adhesion molecule-1 on human mucosal microvascular endothelial cells to an extent similar to the combination of interleukin -4 and tumor necrosis factor -α . It also promoted adhesion of eosinophils isolated from patients with allergic rhinitis to these cells.

No induction of adhesion molecules was observed with the VOCs; 1,2-, 1,3-, or 1,4- benzene; o-, m-, or p-xylene; or toluene at the same concentration. These observations might explain the finding of an increased number and proportion of eosinophils in nasal lavage fluid of healthy volunteers up to 18 h after exposure to 0.5 mg/m3 of formaldehyde for 2 h . In Swedish school personnel, formaldehyde concentrations were significantly associated with decreased nasal patency and increased levels of the inflammatory markers eosinophil cationic protein and lysozyme, but not myeloperoxidase, in nasal lavage . There are increasing indications that formaldehyde not only affects the upper respiratory tract but that it can also enhance allergic sensitization and, through this and possibly other mechanisms, can cause lower respiratory tract symptoms, including asthma. Formaldehyde has been shown to enhance sensitization in ovalbumin -immunized guinea pigs . Although chronic inhalation of formaldehyde does not appear to induce significant inflammation in the lower respiratory tract of non-sensitized mice or guinea pigs , it has been shown to increase the number of inflammatory cells in bronchoalveolar lavage fluid of OVA-immunized mice and to potentiate allergen-induced bronchoconstriction in OVA-immunized guinea pigs . Occupational or accidental exposure to formaldehyde occasionally has been associated with the development of asthma that can persist even after further exposure to formaldehyde is avoided . In some of these cases, specific inhalation challenges identified formaldehyde resin dust, but not gaseous formaldehyde, as the cause of asthma symptoms . Whereas formaldehyde gas is largely absorbed in the upper respiratory tract, formaldehyde in particulate form could reach the lower respiratory tract, which could explain its greater ability to cause airway responses. Because products made from urea–formaldehyde resins, such as particleboard and medium-density fiberboard, are used extensively in the construction of new houses, formaldehyde resin dust may also be in residential environments. Although wood products are the sources that emit the highest amounts of formaldehyde, a wide variety of other products also contribute to indoor formaldehyde pollution .

ETS is another important source of formaldehyde. Mean or median residential indoor formaldehyde concentrations of 15 to 30 µg/m3 have been reported in several recent studies from the United States and Australia . Maxima ranged between 139 and 408 µg/m3 , indicating that some homes largely exceed current indoor guidelines . Notably, with increasing awareness of the adverse health effects of formaldehyde, the guideline values have been steadily decreasing. Currently, the lowest guideline value is the chronic inhalation reference exposure level of 3 µg/m3 set by the Office of Environmental Health Hazard Assessment of the California EPA. Chronic relevance exposure levels are concentrations or doses at or below which adverse health effects are not likely to occur. Despite the relatively low concentrations of formaldehyde in homes compared with occupational exposure levels, chronic domestic or other indoor exposure to this chemical can result in sensitization to formaldehyde itself and can enhance the incidence and severity of atopic sensitization to common allergens . Importantly, residential formaldehyde exposure has been associated with inflammation of the lower respiratory tract as well as asthma and other lower respiratory tract symptoms in children and adults. Concentrations of exhaled nitric oxide , which is believed to represent a marker of pulmonary inflammation, were found to be significantly higher in healthy children age 6 to 13 yr who were exposed to residential concentrations of formaldehyde of 50 ppb or greater compared to those exposed to levels less than 50 ppb . The technique used in this study ensured that the exhaled NO originated from the lower respiratory tract. This suggests that formaldehyde exposure may have induced an inflammatory response, even in children without signs or symptoms of upper or lower respiratory tract disease. The prevalence of asthma and chronic bronchitis was significantly greater in children, but not adults, from homes with formaldehyde concentrations greater than or equal to 60 ppb compared with those exposed to lower levels . A linear decrease in peak expiratory flow rates was observed with increasing formaldehyde exposure. A study of Swedish adults found significantly higher levels of both VOCs and formaldehyde in connection with indoor painting within the last 12 mo, and, in turn, exposure to recently painted surfaces was associated with increased symptoms related to asthma and current asthma as well as at least one asthma-related symptom in adults .In young children who were discharged from the emergency department with asthma as the primary diagnosis, there was a significant association between case status and higher residential formaldehyde exposure compared with age-matched controls .

In the same group of children, a significant correlation was also detected between total and individual domestic VOC levels and asthma; benzene, ethylbenzene, and toluene were each associated with significantly increased ORs . Note that it is difficult to determine whether wheezing illness in such young children truly constitutes asthma. Total VOCs measured in 96 Japanese homes carried significantly elevated ORs for throat and respiratory symptoms in the 317 residents of these buildings . Xylene, α-pinene, and nonanal were the three individual VOCs significantly associated with these symptoms. An association between VOC exposure and asthma has further been suggested by the finding that urinary concentrations of muconic acid and 1-hydroxypyrene were elevated in children with asthma compared with children without wheezing episodes or atopic diseases . In partial contrast, in a study of 193 children with persistent wheezing illness and 223 controls age 9 to 11 yr, no association was detected between formaldehyde or individual or total VOCs and case status . However, the frequency of nocturnal symptoms was associated with formaldehyde exposure but not with VOC concentrations. In Swedish adults, cannabis grow equipment nocturnal breathlessness was significantly associated with both the formaldehyde and the VOC concentrations in their homes . Residential formaldehyde exposure was not significantly associated with the risk of asthma or respiratory symptoms in a group of 148 Australian children age 7 to 14 yr, although the maximum recorded formaldehyde values of four 4-d samples were associated with atopic sensitization . Note that this is one of the few studies in which exposure was measured on several occasions through the year. In most studies, only single measurements of formaldehyde and/or VOCs were taken. Therefore, in our opinion, the associations with allergic sensitization or asthma observed in such studies should be interpreted with considerable caution. The limited data available indicate that there are substantial day-to-day, daytime vs nighttime, and seasonal fluctuations in VOC exposure resulting not only from changes in the environment over time but also from differences in sources and activities that result in exposure . Intra-individual variation over multiple monitoring periods was found to span two orders of magnitude for each of the 14 VOCs measured in personal air . Additionally, residential indoor VOC concentrations are consistently lower than levels measured in the personal air space of both adults and children , indicating that they do not fully reflect personal exposure. Furthermore, it is not clear whether peak exposure or chronic low-level exposure constitutes a greater risk for atopy and asthma. Concentrations of indoor VOCs and formaldehyde generally exceed outdoor concentrations by as much as an order of magnitude . This clearly shows that they are emitted from indoor sources and are not transported in from the outside. Sources, rather than types and rate of ventilation, were associated with indoor formaldehyde, VOC, CO, and NO2 levels in homes . This was at least partly confirmed by a Finnish study of VOCs that combined personal exposure assessment with measurements in residential and work environments . ETS was found to be a dominant source of personal VOC exposure. In ETS-free homes, variability in VOC exposure stemmed from compounds associated with cleaning products, followed by compounds associated with traffic emissions, long-rangetransport of pollutants, and product emissions . Together, these data suggest that source control constitutes the most effective way of reducing environmental exposure to formaldehyde and VOCs.Phthalates are dialkyl- or alkylarylesters of 1,2-benzenedicarboxylic acid.

The major representative is di phthalate , of which the worldwide annual consumption exceeds two million tons . Waste that contains DEHP is estimated to emit another 100,000 tons of DEHP annually. Total worldwide phthalate consumption is estimated at 3.25 million tons. DEHP and other phthalates are used as plasticizers in polyvinyl chloride products, which may contain up to 40% DEHP. PVC resins are used to manufacture a wide variety of items, including floor tiles, vinyl upholstery, toys, disposable medical examination and surgical gloves, medical tubing, blood storage bags, components of paper, and paperboard. Additionally, phthalates are used as fixatives, detergents, lubrication oils, and solvents as well as in cosmetics and personal care products. Because phthalates are not covalently bound to PVC-based products, they leach and vaporize from plastic over time.The main exposure route is generally assumed to be ingestion, with fatty foods, such as dairy, fish, meat, and oils containing the highest levels, whereas inhalation and dermal contact make lesser contributions . However, in the case of diethyl phthalate used in personal care products, dermal absorption can probably substantially contribute to total exposure. Recently, the detection of several phthalate metabolites was reported in human breast milk, indicating that oral exposure can begin immediately after birth . Additionally, direct intravenous exposure occurs in patients undergoing dialysis or receiving blood transfusions. Note that there is limited evidence to support the hypothesis that food constitutes the major source of phthalates . Rather, a recent study found a significant correlation between the concentrations of di-n-butyl , butyl benzyl , and DEP in inhaled air and their urinary monoester metabolites . Correlation coefficients ranged from 0.65 for BBzP to 0.42 for DEP. Substantial amounts of various phthalates were also found to be adsorbed to suspended PM and may make even greater contributions to inhalation exposure than phthalates in the vapor phase . Together, these results suggest that inhalation may represent an important exposure route for at least some phthalates. Tables 4 and 5 summarize measurements of various phthalates in air and dust of residences, schools, and day care centers. The ubiquity of phthalates and the resulting high level of contamination of laboratory equipment made it difficult to assess the extent of exposure until measurement of monoester metabolites was introduced . After oral ingestion, phthalate diesters are hydrolyzed to their respective monoesters. The relatively polar and low-molecular-weight phthalates are excreted primarily as monoesters. The monoesters of phthalates with higher molecular weights, such as DEHP, di-n-octyl phthalate, and di-isononyl phthalate, undergo rather extensive ω-1 and ω-oxidation of their aliphatic sidechains . In humans, monoesters and the oxidative metabolites are excreted primarily as glucuronides .

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Five species had a meaningful space use response to cannabis farms

Private land sites may use high-powered grow lights, drying fans, and visual barrier fencing, which could create potential wildlife disturbance . Such practices are less common on public land. It is possible that as cannabis production expands, particularly in the licensed industry, these forms of indirect impact may be more typical of cannabis production overall. Indeed, indirect effects of production practices on wildlife space use and behavior is a common concern for other agricultural crops , and may also interact with direct effects on mortality . Therefore, it is critically important to study both indirect and direct effects of cannabis on wildlife communities, particularly on private lands where research is lacking. Because outdoor cannabis farming is a land use frontier and therefore often characterized by different land use practices and patterns from traditional established farming in the US, it is uncertain whether other agricultural systems provide the best models to predict wildlife responses to cannabis development. Wildlife may use, avoid, or display differential responses to cannabis development, depending on whether production more resembles small scale countryside farming , industrial agriculture , or exurban/suburban development . In the case of differential responses, it’s also unclear whether cannabis production would have widespread enough effects to trigger mesopredator release , or generate novel food sources that could be exploited by behaviorally adaptable species like omnivores and small mammals . The small-scale, private-land cannabis farms for this study included one licensed recreational production site, one medically licensed production site, and six unlicensed sites. All farms were producing cannabis for sale, though in different markets depending on their access to licensed markets. We also had cameras placed in three hemp fields next to cannabis farms. We selected these eight cannabis growing equipment farms because they: were representative of the size and style of cultivation predominant in Josephine County in the years immediately following recreational legalization in 2015 , were all established after recreational legalization except for the medical farm, did not replace other plant-based agriculture, granted us permission to set up cameras on site, and were located next to a large section of unfarmed land that could grant researchers access in order to place cameras across a gradient of distance to cannabis farms.

Our sampled farms were small , had conducted some form of clearing for production space, and three had constructed some form of fence or barrier around their crop. Nonetheless, specific land use practices and production philosophies differed between farms . We cannot disclose farm locations, as per our research agreement for access. Monitored farms were clustered within each watershed: one farm in Slate Creek, five in Lower Deer Creek, and two in Lower East Fork Illinois River; however, most farms were also located near other nearby cannabis farms that were not directly monitored in this study. We placed unbaited motion sensitive cameras on cannabis farms as well as in random locations up to 1.5 km from the monitored farms. This is an expansion on previous camera research that only assessed on-site wildlife at these same farms . We placed cameras approximately 0.5 m off the ground to capture animals squirrel-sized and larger. We set cameras to take bursts of 2 photos, with a quiet period of 15 seconds. To guide the placement of cameras, we overlaid the area surrounding each cannabis farm cluster with a 50 x 50 m grid and then selected a random sample of at least one quarter of grid cells . We selected a 50 x 50 m grid size because we wanted to be able to detect fine scale space use responses of wildlife. The random sample was stratified by vegetation openness and distance to cannabis farm in all watersheds, and additionally by distance to clearcut in the Slate Creek watershed, such that cameras were placed in proportion to the landscape attributes and a distance gradient was achieved. When a selected site was inaccessible, we selected a new one that also met the same stratification criteria. We rotated 15-20 cameras through the sampled grid cells, ensuring each camera was deployed for at least one round of two week duration. Because of rotations and field constraints, all cannabis sites were not monitored at the same time or for the same length of time . Altogether, we monitored a total of 149 camera stations for a combined 4,664 trap nights. We then used a team of researchers trained to identify species found in the study area to sort photos by hand, grouping by species. We calculated spatial and descriptive covariates for each site to use in wildlife occupancy and detection models . First, we calculated spatial distance covariates. Our main covariate of interest was distance to cannabis farms.

To calculate distance to cannabis, we combined the location data for participating farms in our study with mapped data on Josephine County cannabis farms from 2016 aerial imagery . Then we calculated the minimum distance from each camera to its nearest farm using the package sf in R. We transformed distance to cannabis using a square root to help fit potential thresholds in wildlife responses. Next, we again used the sf package, this time to calculate the distance from each camera to the nearest major paved roadway, which was primarily highway 99 for most sites. For our two raster-based covariates, we used the raster , and exactextractr packages in R. We calculated the proportion of forested land cover within a 50 m buffer around each camera, and extracted the elevation in meters at each camera site. We also included some non-spatial covariates. We included a covariate for Julian date of each interval, as well as Julian date squared, to capture seasonal peaks. We then included an estimated distance at which a camera could still detect an animal , which was measured at camera setup. We also generated activity indices for dogs and humans by calculating the number of observations of humans or dogs, respectively, at each camera within the last three days, divided by the number of days the camera was active. This produced an activity rate where the beginnings or ends of placement rounds were on the same relative scale as all other days. All continuous variables were scaled so that they centered on 0 with a standard deviation of 1 and checked for correlations in R. Finally, we used additional categorical covariates to account for potential effects of geographic region and camera type. We assigned each camera a binary region variable based on which USGS Unit 12 watershed it was located in, such that Region1 represents Lower Deer Creek, Region2 for Lower East Fork Illinois River, and Region3 for Slate Creek. We created a binary variable for camera type. We gave a 0 to camera models that generally performed well in our study system and a 1 to camera models that generally seemed to perform worse or were older models .To assess the local space use response of wildlife to cannabis production, we used single-season, hierarchical single and multi-species occupancy models. Our approach is a departure from the typical use of these models to estimate occupancy in that we knowingly violated multiple assumptions of occupancy models: first, because cameras were spaced relatively close together compared to the home range of species included in the study, we have likely violated the assumption of independent cameras; second, as a result of the aforementioned spacing as well as sampling across two years , we likely violated the model’s assumption of geographic and demographic closure . We have done our best to account for these violations in our use of regional fixed effects, as well as our narrow interval of replication . However, given our interest was in space use associations and not estimates of occupancy, we believe the violations are a minimal issue. This use of occupancy models is not particularly unusual, as the use of occupancy modeling to assess space use is becoming more common in wildlife response studies, and even traditional uses of occupancy modeling are influenced by wildlife space use .

With the closure assumption violated, the occupancy probability estimate represents the likelihood that the animal occupied the site at any point during the study period, while the detection probability represents a combination of the probability that the species is detected and the intensity of use of the site within its larger range . This interpretation is common in camera trapping studies , but we proceed while being careful to acknowledge where appropriate that any covariate’s influence on detection probability is a combination of its effect on detection and the intensity with which an animal uses a given space. In addition, we have taken care to include variables in the detection process to account for what we anticipate to be the largest sources of variation in detectability, so that the other variables should primarily reflect space use intensity. We therefore interpret occupancy for the models as space use rather than true occupancy . We operationalize detection as a combination of intensity of use, and camera detectability or error . To examine animals’ space use in relation to distance from cannabis grow table farms, we first conducted single species occupancy analyses on nine wild and one domestic species . We summarized species observations on and surrounding cannabis farms and created detection histories using the package CamtrapR in program R using Rstudio . We used a 24-hr time interval because our focus was on estimating space use associations instead of occupancy , and a short interval reduced the likelihood of the same individual animal being detected on neighboring cameras . We modeled the space use probabilities of the most commonly detected species or those of particular ecological interest, including: black-tailed deer , black bear , bobcat , coyote , gray fox , black-tailed jackrabbit , striped skunk , California ground squirrel , tree squirrels , and domestic dog using the NIMBLE and nimble Ecology packages in Program R . We selected these species because they had sufficient detections to model , and because they covered a range of functional groups, including predators and mesopredators , omnivores , large and small prey , and a domestic predator . We included dogs as an added check on our modeling approach, as their general distributions and associations are already well known in the study system, unlike wildlife species. We modeled the observed data as a binary variable where 1 was an observation for a given species at camera station s, and 0 was a non-detection. We modeled the observed data for each species as a product of both true occurrence of a given species at a site and our probability of actually detecting it , which is also influenced by intensity of use at a given site. The model assumes that true occupancy is an outcome of a Bernoulli-distributed random variable, denoted zs~ Bern, where is is the probability that a given species used site s on any day during the survey period. We assumed that occurrence and detection probabilities varied by species, and that cannabis might influence both in different ways. For occupancy, we expected that increasing distance from cannabis farms would increase animal space use for all species except domestic dogs, and ground squirrels. We also expected that elevation and forested land cover would influence space use based on their importance in other wildlife studies . We expected distance to highways to negatively affect space use, and to function as a proxy for other non-cannabis forms of human land use in our study system. While we initially wished to include distance from clear cuts as the other major source of human disturbance in the study system, it was highly correlated with distance to highways, so we did not include it in our models. Finally, we accounted for potential regional differences in the three watersheds by including a fixed effect of region. We parameterized regional fixed effects using region-specific intercepts as described in the following equations. For the single species occupancy models, occupancy and detection varied by species . Recall that for our models, we are interpreting occupancy as space use, and detection as a combination of detectability and space use intensity .

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Our results indicate a large overlap of cannabis farms with areas of high projected fisher occupancy

See the supplement for a more local comparison in which we calculated the proximity and overlap metrics for all parcels within a buffer around each cannabis site. For buffer size we used the average home range of fishers from southern Oregon. Outdoor cannabis production across Josephine County in 2016 was generally small-scale but also pervasive, and suggested that recreational legalization greatly expanded the industry locally. We mapped nearly 4,000 individual gardens and greenhouses on 2,220 different farms, all identified as highly likely to be cannabis . Most sites were new since legalization . Most production was in outdoor gardens , but a greater proportion of greenhouses were new . Farms contained an average of 1.76 individual sites, with a maximum of 14. The average size of individual sites and farms was small but highly variable in terms of cultivated area and number of plants . The average parcel size for farms was 0.098 km2 . 99.6% of detected farms were on private land parcels. Out of all private land parcels in the county, 5.7% contained a farm identified as highly likely to be cannabis. Cannabis sites were clustered at multiple spatial scales. The Ripley’s K analysis indicated that cannabis sites were clustered at all observed spatial scales . At the county level, the Getis-Ord Hotspot maps identified two regional hotspots near Williams in the SouthEast, and in the Illinois Valley in the South-West . The sub-watershed analysis indicated that even within these larger regional hotspots, there were pockets of more and less intensive production . Both the county and sub-watershed hotspots seem to follow primary roads or river networks.Overall, cannabis was produced on more undeveloped and forested parcels compared to all available private lands as a whole . The most common land cover for individual outdoor gardens was shrubland , followed by cultivated , and forest . Greenhouse cannabis production occurred in areas already cultivated with other crops , followed by shrubland , and forest . At the farm scale, however,hydro tray where outdoor and greenhouse production was combined, forest was the most common land cover type .

The predominance of cannabis in forest and undeveloped land covers was also supported by the Gradient Nearest Neighbor data on forest structure. Although the GNN dataset uses a broader categorization for forest, it also indicated that cannabis was disproportionately grown in forested areas . Nevertheless, the forest structure of farms was similar to that on all available private parcels . Cannabis farms occurred in areas with intermediate carnivore richness, similar to all available private parcels . However, at the individual species level, cannabis farms overlapped with higher projected fisher and ring tail occupancy, and lower gray fox occupancy . These differences were consistent across land cover, forest structure, and zoning. However, median fisher occupancy values were larger on high elevation parcels, and a greater proportion of cannabis farms were at higher elevations compared with private parcels. There was no difference in richness between existing or new cannabis farms, and no difference at the species level except for gray fox, which had a slightly higher median occupancy on existing farms compared with new farms .Cannabis was located slightly closer to rivers compared with all available private parcels, though the interquartile range intervals overlap . There were also a higher proportion of cannabis farms located within 15 m of a river or stream, compared to private parcels . However, the proximity of farms to threatened fish species was mixed. For example, although there was a large variation in distances and overlap of IQR intervals, on average cannabis was nearly 1.5 times closer to coho salmon habitat than all private parcels, yet more than 5 times farther from spring chinook habitat. The variation in proximity to fish habitat may be in part due to the proximity of cannabis to smaller streams by order . This study is one of the first landscape-scale assessments of small-scale outdoor cannabis farming and its potential broad-scale ecological effects in a rural biodiversity hotspot. Our results suggest two main conclusions. First, private land cannabis farming in Josephine County, Oregon in 2016 was common and spatially clustered, expanded post-recreational legalization , and yet only covered a small portion of the total land area.

This supports our expectation that cannabis farming in Josephine County would exhibit characteristics typical of the legacy development pathway, but that these farms would largely be new post legalization. Second, our spatial proximity results highlighted areas of overlap or proximity of cannabis farms and sensitive habitats and species. Compared to the surrounding context of all available private land parcels, cannabis was more frequently located in forested areas and undeveloped land, closer to rivers/streams and coho salmon habitat, and in areas of high value as fisher habitat. These results provided mixed support for our expectation that cannabis production would be in areas that increase its potential ecological impact. Recent research on public land production in the broader region highlights similarities and differences between public and private land production. For example, both seem to be located relatively close to rivers and streams, with ~50% canopy cover, and in relatively young stands . However, while we may presume that all production on public lands represents new clearing for production, our results indicate that 32% of farms are on already developed and unforested parcels. Additionally, public lands provide critical refuges for many of the region’s carnivores, which may help explain why public land production appears to overlap more with carnivore habitat than our results for private land production . Perhaps most importantly at a landscape scale, farm size and total extent appear to be much smaller for legacy pathway private land cannabis mapped in this study compared to estimates of public land production practices . Despite the differences between public and private land cannabis production, private land cannabis farming still has characteristics that warrant continued research and planning. Our results suggest that legacy pathway cannabis farming could be compatible and comparable with existing rural land use in Josephine County. In order to ensure this continues to be the case, however, further attention should be given to conservation outreach, policies to support small scale farming, and attention to land use practices on farms, particularly those that may affect carnivores and coho salmon. As the industry continues to expand, policymakers and conservationists need to clarify landscape level strategies to ensure a sustainable future.

Care should be taken when interpreting these results, since cannabis agriculture takes many forms and often exhibits regional differences in production practices that may influence its ecological impact . Our study, by nature of our mapping approach, evaluated outdoor production on private lands. We were unable to quantify whether the farms we mapped were illegal or licensed medically or recreationally, nor how many farms we may have missed by farmers effectively concealing their crop. Given our mapped sites included 2,227 farms in 2016 compared to the 43 recreationally licensed locations in 2016 , it is likely that most of the farms we georeferenced were not licensed. If this is the case,planting table the lack of effort to conceal crops is notable. We suspect because cannabis was pervasive , that enforcement would not have been feasible . Therefore, we were confident that our study accurately quantified the distribution of private-land cannabis production because of the visibility of both licensed and unlicensed farms from aerial imagery. Further, our data likely does not capture all of the cannabis being grown in Josephine County as we were unable to quantify concealed farms on public land or indoor cannabis production. Instead, our study offers critical insights into the ecological consequences of the growing industry in legacy production regions. The overall cultivated area of private land cannabis agriculture at the landscape scale in Josephine County in 2016 appears to be similar to small-scale rural development already occurring regionally. For example, in a county of 4,250 km2 , the total cannabis cultivation area was only 1.34 km2 . This small size is similar to other agricultural production in the county: in 2017, Josephine County produced 2.98 km2 of grapes and 0.48 km2 of vegetables . Cannabis in Josephine County was also considerably smaller in scale than other legacy cannabis-producing regions in Northern California in 2016, where averages ranged from 53-119 plants per site, compared with the median of 21 found in our study . While we do not have comparative research on the ecological effects of other agriculture in the study area, small-scale agriculture in rural areas often creates a landscape mosaic that supports species richness . The ability of small-scale cannabis farming to function like agriculture in other working lands systems, however, requires a deeper understanding of land use practices associated with cannabis production. Specifically, to be ecologically sustainable, small scale private land cannabis farms would need to create a significantly smaller ecological footprint than public land cannabis . Although the area of cultivation for cannabis in Josephine County was small, this study did not evaluate the edge effects of cannabis cultivation, nor take into account other forms of disturbance associated with the sites, such as clearing beyond the cultivated area, road construction, or water storage development. Therefore, the actual overlap and potential ecological effect from cannabis farming in the region is likely to be larger than what was documented in this study. Our understanding of these broad scale impacts would be enhanced in future studies that may be able to assess the fine scale response of wildlife on and surrounding cannabis farms.

While our study does not address direct effects of cannabis production, we did identify spatial relations of cannabis development that could pose unique risks to terrestrial and freshwater ecosystems. We found that cannabis production was clustered in its distribution, which is consistent with research from northern California . This clustering could be an ecological concern if cannabis is occurring disproportionately in sensitive ecological areas. Similarly, the proliferation of fences associated with cannabis could be a concern for habitat fragmentation as the industry expands . The overlap results indicate that cannabis may be grown disproportionately in forests and at higher elevations, which suggests cannabis could be associated with greater land clearing than other development on private parcels. However, the forests where cannabis was grown did not appear to be denser or older than comparable parcels.This overlap was greater on cannabis farms than private land generally, but could be due to a higher proportion of cannabis farms located at higher elevations . However, elevation alone doesn’t explain this overlap. Fisher occupancy was projected to be higher on cannabis farms than the areas immediately surrounding them . This suggests that even at fine scales, farms are appearing in areas of potential for high quality habitat for fisher. What this overlap may mean for fisher populations is unclear, given the lack of research on the impacts of private land cannabis production. Private land cannabis has not been documented to have the same negative effects on fishers as public land production, and in particular pesticide and toxicant use appears to be lower on private land farms, according to self-reported farmer surveys . However, anecdotal reports and local news stories raise concerns for these private land farms as well, and many grower organizations have emphasized a need for stronger environmental norms among farmers. Given the remaining uncertainty, these results emphasize the potential need for conservation attention to private land farms as well. Surprisingly, the individual species differences did not add up to differences in overall carnivore richness, which was relatively consistent across the study area. This raises the possibility that the differences in carnivore distributions might be driven by competitive interactions , though finer scale research would be needed to disentangle the drivers of these species distribution patterns in relation to cannabis production. Regarding potential interactions between cannabis production and freshwater ecosystems, the picture was also somewhat mixed. There were a number of farms within 15 m of rivers and streams, but this was not surprising given the high density of rivers and streams in the study area. On average, most farms were only slightly closer to rivers and streams than the surrounding context of all private land parcels.

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Farmers with low human agency and low access to assets struggle to survive every cold night

The lack of indoor thermal comfort brings farmers to use their kitchen for warmth, and the lack of well-designed kitchens in the region creates health complications for many farmers and their families. Distributing blankets and food should not be the sole response to such conditions. Long-term solutions are needed to abolish the never-ending cycle of the harmful effects of cold temperatures in the region. The optimal solution would continue using reactive approaches, such as humanitarian aid when needed, but add to those a focus on creating robust long-term proactive approaches to improving indoor thermal comfort in the region.When talking about impacts related to low temperatures, the primary concerns are due to social vulnerability and a lack of resources. However, impacts related to drought are complex and go beyond social vulnerability. Governance, access to water, good quality of wells, and other methods of collecting water are of great importance. The information provided by different agencies can be contradicting and confusing at times. Access to certain kinds of information alone does not provide everything that leaders need to understand what is happening on the ground and everything farmers need to adequately prepare for drought. Dealing with drought-related impacts would benefit from a stronger network of information and improved methods of transmitting a concise and less confusing message to stakeholders . Both qualitative and quantitative analyses point to concerns about social capital in the region and indicate the need for a stronger understanding of the role of social networks in vulnerability. Social networks are a critical component of the social capital that protects against vulnerability,grow tray stand but vulnerability assessments often reduce social networks to an asset.

These assessments rarely study how social networks can aid members to cope with a crisis, including finding alternative livelihood strategies. Furthermore, a binary approach to social network is problematic, because while membership bolsters trust and access to resources, the distribution of such benefits are uneven across specific networks and specific positions within a network. A network does not benefit all its members equally, nor does each network benefit its members equally. These variations raise questions about how to measure network interactions in vulnerability assessments. Should social networks even be included as part of social capital? Should social networks be treated as a new component of vulnerability that connects entities forming such networks? I included social networks only as an asset in this dissertation, but the qualitative results suggest that more effort should be focused on how best to include social network structures and connectivity in spatial vulnerability assessments. Mapping social vulnerability indices allows areas of extremely high or low vulnerability to emerge. However, vulnerable populations remain unseen at certain levels of aggregation. The level of analysis optimal for decision-making likely varies according to who the information is aiding and the purpose of the analysis. Therefore, a single correct scale of analysis cannot be suggested. This brings interest to the uses of an interactive interface to study vulnerability at multiple scales rather than the typical static map for assessing vulnerability. The results of the present research suggest the value of a more detailed look into the impacts that result from weather-events of less intensity and duration. Social vulnerability might be strongly spatially associated with such impacts. Also, the reason that socioeconomic vulnerability indicators are spatially associated with some aspects of topography is unknown, and this association clearly deserves further study. The geon methodology creates homogenous areas that do not necessarily follow administrative divisions. Region officials can use these maps to address concerns at the level of phenomena and not just according to imposed administrative boundaries.

Many cases showed homogeneity in vulnerability indicators across neighboring municipality boundaries. In such cases, municipalities can work together with neighbors to address similar concerns. However, patterns linked to administrative boundaries are present in some of the geon maps. For example, physical and social capital present two neighboring geons at both extremes of the index values. When municipality boundaries are added to the map, it is revealed that the boundary separating the geons coincides with the municipality boundary. Therefore, while it is quite valuable to map vulnerability according to the boundaries of phenomena instead of administrative boundaries, in some circumstances, the boundary patterns do coincide. In su, this dissertation demonstrates how qualitative and quantitative research methods can build on each other to create a more comprehensive assessment. With the increase in the uncertainty due to weather and climate hazards, using ethnographic approaches to understand the local context is imperative. Such methodologies could act as a bridge that connects local understandings with a multitude of stakeholders and scales. Results from this dissertation have the potential to serve as scaffolding for future adaptation strategies in Puno and, eventually, in other areas less developed parts of the world where agriculture provides the main livelihood. Ethnographic components of these research provide an in-depth understanding of the location; however, they possess transferability. The results from this dissertation could be transferable to the study of social vulnerability in other high mountainous regions or rural environments.While the Japanese islands have been prone to a variety of natural disasters throughout their history, the magnitudes of some of these omnipresent threats are observed to have increased in recent years. My informants, for example, anecdotally spoke of perceived increase in the temperature throughout the years.

The relatively cool rainy season which lasted from the middle of June into July, which used to require heating equipment, turned into “wet summers.” They also talked about orange trees they planted that used to produce sour Hlavors now yielded sweeter Hlavors presumably due to the warmer climate. Relatedly, storms of many kinds are reported to have intensiHied in recent years. In the past, the term tornados were unheard of, but today they are new and frequent occurrences. Other severe storms are accompanied by larger hails than in the past. In fact, in the winter of 2014, the year this Hield work took place, the eastern Japan, including Tokyo, experienced record-breaking snowfalls. As a result, many of the informants’ green houses were destroyed. Yet the informants appeared composed and nonchalant about the effects of these changing climates on their food production. Most of them did not bring up the topic during the interviews until they were asked specifically about it. What could be some of the reasons for this? For one,garden racks wholesale the general increase in temperature and the intensity of the rain and snowfall has not significantly affected the informants’ “outdoor crops,” which are predominantly rice and wheat. The majority of other products, mainly vegetables, are produced indoor. The destruction of the green houses due to the record amount of snow was a major loss. Nonetheless, the informants seemed to have accepted the incidence as a by-gone, and showed a sense of gratitude toward the Japanese government, which helped cover about ninety percent of the loss. Such is a reminiscent of the way the people of northern Japan reacted calmly to the calamity of the tsumani in 2011 . What implications do these preliminary observations offer in terms of “cultural models” of nature that are purported to have influenced the informants’ narratives about food production? I hypothesize that the informants relied on an overarching cultural model that nature can be “humanized” to enhance human endeavors particularly in the areas of self-cultivation and associated interpersonal relationships. Using this cultural model works as a buffer against and around which to circumvent the perceived and real harms of raw, untamed nature. According to this cultural model, raw nature is un-natural. Nature is “natural” only when it is humanized to enhance human existence and activities . Since Japan is a highly industrialized society with complex economic systems, none of the informants engaged in subsistence farming. As such, their farming did not rely directly or solely on naturally given soil conditions or weather patterns. Instead, they utilized advanced in-door food productions facilities and technologies. They also took advantage of the wealth of current, and research-based farming knowledge provided by the municipal and national farmers organizations such as JA, Japan Agricultural Cooperatives. They also exchanged ideas and tips with other farmers, which they acquired through experience or the sources mentioned above. As to what makes plants and animals grow, informants shared basic knowledge which they saw as fundamental to successful farming: i.e., knowledge about optimal soil conditions , lights, winds, temperatures, timing of planning and harvesting and other maintenance activities , and ways to prevent diseases. They said that such knowledge comes from experiences, from other farmers including their parents and family members, and from the government-based, local and national farming bureaus such as JA. No one mentioned supernatural factors such as “gods” or “spirits” as factors contributing to the growth. In terms of their commercial success, informants revealed two distinctive yet complementary models. The first model may be called ‘rational and profit-oriented.’ Here the food producers worked in concert with the information provided by JA about the crops and seeds types, kinds of diseases that are prevalent and how to prevent them to maximize their productivity.

The JA’s also organized chains of marketing outlets into which the farmers could distribute their product at a timely fashion. Most of the large-scale rice, wheat, tomatoes, plums and pears farmers relied on such support system. The second model may be termed ‘non-rational and relational,’ and even ‘moral’ and ‘spiritual,’ in a sense that it seeks higher level of meaning and satisfactions from farming than merely profiting from it. Informants often used the terms kodawari and tsunagari to express this view. To kodawaru means to produce foods that bear one’s ‘signature’ heart/effort. Many of the consumers who tasted such foods become ‘repeaters,’ loyal customers who develop a special and lasting tie to the food producers. Many famers noted that they gain most satisfactions out of their job from such special relationships. In short, the first model is essential because without it, farmers cannot sustain their livelihood. The second model complements the first as it helps them to create deeper and more personalized meaning out of their work. Below are some examples of the second perspective from the semi-structured interviews and the nature walks. Michiko Sekiguchi, a sixty-four year old woman, married into a multi-generational farming family. While her husband takes charge of the rice and wheat, which supports family’s main income, she grows greenhouse tomatoes, along with a variety of other green vegetables. She says her operation is “small and not profitable,” but had continued it for the last eighteen years. Asked why, she responded, “It’s [my] kodawari.” Asked to explain what kodawari means to non-Japanese, she said, “it means to be particular [about your mission] and not to compromise .” In a practical term, “it means to…wake up at three or four in the morning every day” to take her vegetables to the local stores. “That way, people say when they eat my vegetales, oishii! . I pick them first thing in the morning and have people eat that way. I especially want young children to know how great they taste.” Another expression of Michiko’s kodawari, in addition to always hand delivering her vegetables fresh, is the farm stand she created for herself, which she named, Daichi No Megumi , which happens to be the brand name given to the rice they produce. The space is filled with wall hangings and gifts she received from her friends. Many of them contain words of appreciation for the relationships they cultivated over the years. Secondarily, she sells the vegetables she produced at low prices. She said that the room symbolizes her connection with other female farmers. It is also worth noting that this farm stand is located next to the family grave. Michiko is grateful that she and her husband inherited the land from their ancestor. She says, “I know how our ancestors were attached to this land, so I would never let it go. When I think of their feelings, I, too, cannot let go of this land.” During our ‘nature walk’ around the family grave, she said, “this [having the grave next to their farm] is a reminder that our ancestors are always watching over for us.” Shinji Amada is a thirty-two year old pig farmer who also took over the business from his father, who inherited it from his father forty years ago.

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Farmers performed religious rituals to attract rainfall to the area

It is coordinated with the arrangement of doors and windows, to avoid any heat leakage. The improved kitchen, as mentioned before, is implemented to reduce health related effects. Another project in the region, using the same technology described in the K’ONICHUYAWASI project, is named Mi Abrigo . This is a national project sponsored by the Ministry of Development and Social Inclusion through their national program named the Cooperation Fund for Social Development . As a prevention effort for winter 2017, Mi Abrigo started building houses in December 2016 in three Peruvian departments: Apurimac, Cusco, and Puno. A total of 1,146 houses were modified in 33 communities from 12 districts. The program modified 400 houses in seven communities from four districts of Puno. However, the program is a national one, and the subsequent home modifications for the 2018 winter do not include Puno. The second stage of the program will modify 1,100 houses in 17 districts from four departments outside of Puno. Furthermore, the plans for the third stage that will modify houses for the 2019 winter does not include Puno either. This third stage will modify 980 homes in 14 districts of four departments outside of Puno. The problem with regulating indoor heating is not only a concern for private housing. Education and health facilities also present poor levels of indoor thermal comfort. Many people in the area express concern for the indoor thermal comfort inside hospitals. Their indoor thermal comfort is of greatest concern to the population experiencing childbirth. Education facilities also possess infrastructure and thermal insulation problems. These problems lead to an environment uncomfortable for learning, especially in the morning. Public education comprises 93% of Puno’s educational facilities, and 65% of them are in rural areas. According to regional agencies, 75% of these facilities are mainly constructed with adobe and are considered to possess environments too cold for pedagogy. About 50% have very old-style constructions. The Ministry of Education has proposed to delay the time classes start every morning to aid in dealing with indoor thermal comfort. Furthermore,plant growing stand the national government has campaigned to educate teachers on how to properly close these facilities when they leave in order to maximize the indoor thermal comfort in the mornings. So it is clearly imperative to prevent temperature-related deaths, but focusing only on heatwaves is not sufficient.

Every year, farmers in the Peruvian Altiplano suffer and die due to cold temperatures in the region. Focusing only on heatwaves due to their increasing frequency and intensity around the world is similar to stakeholders forgetting about farmers in specific locations because the world is urbanizing. And temperature-related events do not result only in deaths, but in negative impacts on livelihoods, health, and comfort. People should not have to merely survive cold temperatures, and stakeholders should pay attention to improving indoor thermal comfort. Farmers with low human agency and low access to assets struggle to survive every cold night. Distributing blankets and food should not be the central response to such impacts. Long-term solutions are needed to avoid the repeated return of the harmful effects of cold temperatures in the region. Drought conditions entail a slow onset and combine multiple factors which make its prediction difficult. Some droughts are easy to predict and can be foreseen a month in advance, while others catch decision-makers by surprise. The prediction, report, and quantification of drought-related impacts remain a significant challenge. Unlike other weather phenomena, droughts are not a single distinct event; just a lack of rain does not equate to drought conditions. During my fieldwork campaign, both austral summers reported drought conditions. However, they had different spatial coverage—as seen in Figure 12—regarding the emergencies reported. The first drought had a more widespread spatial coverage and presented a more significant challenge to both farmers and decision-makers. On the other hand, the second drought was more localized, and the difficulties experienced in many aspects of the emergency cycle were at a smaller scale than in the first drought. The prediction of the drought in Summer 2015–2016, including the report of emergencies, was confusing and inconsistent. The national weather service agency provides monthly agrometeorological reports summarizing meteorology characteristics and providing information related to precipitation’s probabilities for the next trimester. Three factors are essential to understand droughts in Puno and their impacts: the agricultural calendar starts in August, the rainy season covers from October to April, and the beginning of the austral summer presents a crucial stage for crop survival. Agrometeorological reports for the three months before the beginning of the fieldwork campaign in January 2016 aid in understanding the complexity of the drought in the region. Predictions in October for the November to January trimester had two scenarios that contradicted each other. Figure 13 presents a prediction with most of Puno experiencing normal precipitation and certain areas experiencing above normal precipitation conditions.

However, the International Research Institute for Climate and Society at Columbia University in New York had different probabilities for the region . These probabilities expressed areas with more than a 50% decrease in precipitation for Puno. Local meteorology reports for November 2015 and December 2015 presented a rainfall deficit of -17% and -19% respectively for the entire department. Moreover, most of the stations were indicating between -20% and -100% of rainfall deficit. Station analysis performed by the regional SENAMHI office in Puno presented similar percentages of rainfall deficit from the start of the rainfall season in October. However, 2015 had only one report related to drought received toward the last week of December. This emergency report mentioned the lack of rainfall in the entire area of the municipality but reported only four hectares of crops affected by the drought. Also, it could be noted that the reported impacts during both austral summers were different from the areas identified to have a higher level of drought risk. Let’s consider the difficulties of predicting the droughts, the conflicting information provided to farmers,the discrepancies in ground experiences in reports, and the farmers’ perceptions. Aside from the discrepancy of the reports predicting normal precipitation conditions versus stations reporting deficits, the region was not expecting extreme drought conditions. The title of a local news article published on December 17 stated that the “drought would be mild in the Peruvian highlands.” The article affirmed that the precipitation would be slightly less than in other years but “according to the experts it will not result disastrously for farmers in the region.” An expert working for INDECI emphasized that if “it is true, according to the forecast of the climate entity, there would not be a drought scenario, the prevention of possible flooding of the rivers should be a priority.” In the same article,plant grow table other experts mentioned the changes in precipitation of -10% to -20% for individual municipalities. Towards the end of December, the Laguna Colorada in Lampa utterly dried up. The Lagoon had been drying for three years due to high daily temperatures and lower precipitation in the area . The representative of the Lagoon area mentioned that on multiple occasions, he presented projects to the provincial government to create a passage from the nearby river into the Lagoon. The provincial authorities emphasized that in November 2015, they brought the case to the Ministry of Agriculture and were expecting a response. As the fieldwork campaign started, available information indicated that drought conditions were expected to be light, and the condition in the Lagoon resulted from a more extended timescale problem. However, the regional ministry of agriculture stated in early January that the drought conditions had affected up to 40% of the crops in the region. Furthermore, farmers pointed out that natural pastures were drying, and farming organizations were asking for oat bales for the animals. Toward the border with Bolivia, in the province of Chucuito, farmers told me stories about current drought conditions and their concerns that it was beyond “abnormal” drought.

They showed dead birds and dead livestock. An elderly farmer cried as he explained to me what was happening: “We are all sad, it makes us want to cry, in June and July there will be nothing; then, this will be dry, and there will be no food for the animals.” The display of farmers crying and showing me dead animals was repeated in various locations in the region. Farmers expressed concern with the availability of natural grassland. The grass available is not tall enough for their animals, and they recounted how it was supposed to be taller this time of the year. Many farmers were alarmed and often revisited stories from 1983. Many farmers did not mention a specific date, but those who did never mentioned anything other than the 1983 drought. Even the regional director of SENAMHI indicated the 1983 drought as a reference while talking about the drought in the area. Everyone admitted that conditions were getting drier every year. But how severe was the 1983 drought for farmers remembering its impacts more than 30 years after? Maps produced by SENAMHI show the Standardized Precipitation Index for a severe drought during the El Niño of 1982–1983 and a more localized drought during the El Niño of 1997– 1998. One of the strongest El Niño events worldwide was experienced during 1997–1998, but the extent of the drought was not severe in Puno. Furthermore, other years with El Niño conditions do not present drought conditions for the region. There is no doubt that the 1983 drought was real and caused numerous problems for the region. However, were the farmers correct in comparing the recent El Niño year with the 1983 drought conditions? During my fieldwork in mid-January 2016, the National Water Authority declared a state of emergency for Lake Titicaca for 90 days. The imminent danger of water deficit in four of the Lake sources of water prompted the decision, a decision praised by the director of the local meteorology agency. Furthermore, smaller towns in the provinces of Chucuito and Azángaro canceled activities that are usually celebrated all over the region. These cancellations, according to local officials, were due to the lack of water in their municipalities. Towards the end of January, Puno’s agricultural sector was declared an emergency zone by the regional agrarian authorities. This decision was necessary due to the loss of up to 60% of the essential crops in the region. The declaration was not only for droughts but included the out-of-season frost and hail that occurred in the region.The month of January ended with a deficit of – 45% of the total monthly accumulated rainfall for the region. Figure 18 presents the anomalies in precipitation per weather station. One can see in yellow the stations reporting from -20% to -60% in precipitation for January 2016. While many stations, in orange, presented from – 60% to -99% in precipitation. SENAMHI also provided a map with SPI to show the depth of the drought for January . Such SPI map patterns and water deficits do not completely explain the occurrence of reported emergencies, as seen in Figure 12. The second drought experienced in the region during my fieldwork campaign had a smaller spatial coverage in terms of emergencies, but below normal precipitation happened in many municipalities outside that area.The level of emergency from the farmers and local authorities was lower than the previous season. The government did not declare a state of emergency, and farmers’ still suffered losses but to a lower degree. The government created and started to work on plans for water management and improvement of water wells in the region. The emergency reports related to drought still do not possess a standardized methodology for explaining impacts experienced on the ground. Many lacks crucial information, making it difficult to use those data for comparison with other social vulnerability indicators. When talking about impacts related to low temperatures, the primary concern is social vulnerability and a lack of resources. But drought impacts are complex and go beyond social vulnerability indicators. Governance, access to water, and good quality wells and other methods of collecting water are of great importance. Furthermore, the information provided by different agencies can be contradicting and confusing at times. Access to information does not necessarily allow leaders to understand what is happening on the ground nor farmers to adequately prepare for drought.

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Many underlying drivers of vulnerability often coincide with the determinants of adaptive capacity

The IPCC’s First Assessment Report , published in 1990, presented a description of the possible vulnerabilities experienced in different domains ; it provided no explicit definition of vulnerability. In 1995, the IPCC’s Second Assessment Report defined vulnerability as “the extent to which climate change may damage or harm a system. It depends not only on a system’s sensitivity but also on its ability to adapt to new climatic conditions” . Later, a special IPCC report titled The Regional Impacts of Climate Change: An Assessment of Vulnerability focused on presenting the current state of vulnerability for each of the world’s geographical regions. The first assessment to dedicate an entire chapter to the conceptualization and operationalization of vulnerability was the IPCC’s Third Assessment Report , published in 2001. Topics mainly focused on impacts and offered only a limited incorporation of the full social-science perspective. TAR was also the first IPCC report to introduce vulnerability as a function of exposure, sensitivity, and adaptive capacity. These were part of the vulnerability framework used in the Fourth Assessment Report in 2007. This vulnerability formulation defines exposure as the degree of climate variation to which a system is exposed. Sensitivity is the degree to which a system is affected by such climate variation. Lastly, adaptive capacity is the system’s ability to adjust to climate variability and extreme weather events in order to moderate potential damages, and to take advantage of opportunities to cope with the consequences . In 2012, the Special Report on Managing the Risks of Extreme Events and Disasters to Advance Climate Change Adaptation introduced a framework that uses a vulnerability interpretation different from previous reports. Vulnerability, according to this framework, does not depend on climate events but is entirely based on pre-existing social vulnerability. Furthermore,greenhouse growing racks exposure does not depend on the hazard but on the amount of population and wealth at risk. This approach became prevalent in disaster management literature, where hazards and exposure areas are well-defined.

The IPCC has stated that the disaster risk-management community has helped highlight “the role of social factors in the constitution of risk, moving away from purely physical explanations and attributions of loss and damage” . It is important to understand the various levels of social vulnerability because they lead to different levels of losses and damages under similar exposure to physical phenomenon . The existing capacity to respond to a hazard predominantly determines people’s vulnerability to natural hazards rather than what may or may not happen in the future . Following this vulnerability framework shift, in 2014, the IPCC’s Fifth Assessment Report reflected significant changes. The IPCC now sees vulnerability as shaped by human conditions; when combined with the hazard it is referred to as “climate risk.” This report moves away from interpreting vulnerability in terms of outcome and toward interpreting it contextually. It is valuable to ask how these two main vulnerability interpretations are different. Approaches to vulnerability assessment are shaped by the interpretations of both natural and social scientists. Natural scientists tend to focus on applying the concept descriptively, while social scientists search for a more contextual explanatory approach. These could be summarized in terms of the two primary interpretations of the vulnerability concept: end-point and starting-point . The end-point interpretation measures future vulnerability descriptively using a top down approach for its assessment. Outcome vulnerability is seen as a residual of impacts minus adaptation. This interpretation expects a linear result wherein projected biophysical impacts on an exposed unit are counteracted by the socio-economic capacity of the unit to take adaptation measures. A commonly used example of an outcome vulnerability framework is the one in the TAR and AR4 reports. However, the latest report and the SREX special report favor a starting-point interpretation for vulnerability. The starting-point interpretation has its origins in the desire to assess social vulnerability and identify changes and the distribution of vulnerability. This contextual vulnerability approach assumes that vulnerability is generated by a diversity of processes, but it is exacerbated by the biophysical impacts of interest . In terms of adaptive capacity, this interpretation assumes that vulnerability determines adaptive capacity. In addition, adaptive capacity is seen to be a part of present-day vulnerability.

Contextual vulnerability is the existing system’s inability to cope with changing biophysical conditions and, at the same time, be influenced by changes in other conditions . As seen in both interpretations, a chicken-or-egg dilemma of order is present with respect to adaptive capacity and vulnerability.In addition, the contextual interpretation tries to focus on the present, while an outcome interpretation concentrates on the future. O’Brien et al. emphasizes that these interpretations are complementary—they conceptualize vulnerability from different perspectives. Assessing all potential points of vulnerability is very difficult. But with the literature shifting away from a primary focus on the biophysical hazard event, stakeholders are increasingly accepting that managing a disaster goes well beyond the hazard agent itself . A greater portion of the resulting disaster is shaped by vulnerability rather than by the hazard itself . Human vulnerabilities need to be an integral concern in the development and assessment of disaster-related policies. Due to the “Babylonian Confusion” when defining vulnerability, this dissertation uses the term social vulnerability to express the vulnerability that encompasses the pre-existing conditions of a location. Since social vulnerability is partly a by-product of social inequalities, it can be defined as “the susceptibility of social groups to the impacts of hazards, as well as their resiliency, or ability to adequately recover from them” . Social vulnerability encompasses an array of concepts, including susceptibility to harm and lack of adaptive capacity . Furthermore, social vulnerability includes disturbances to livelihoods . Rural populations, especially in developing countries, practice livelihoods that directly depend on natural resources . A livelihood involves the assets and activities that combine to determine how an individual or group makes a living . For a livelihood to be sustainable,vertical hydroponic garden it needs to be able to cope with and recover from shocks and maintain or enhance people’s capabilities without undermining natural resources .

Early geographers and social anthropologists performed studies focusing on livelihoods and modes of life . However, such perspectives on development did not dominate the literature until the late 1980s, when interests in livelihoods connected three concepts: sustainable, rural, and livelihoods. Reflecting the complexities of relating these concepts, numerous frameworks that attempted to do so arose in the 1990s. The most popular became the Sustainable Livelihood Framework that resulted from research by Scoones . In the SLF, Scoones addressed issues regarding susceptibility and adaptive capacity to climate variability/change, to a limited extent . It became common to use SLF to measure social vulnerability, especially with farmers and rural populations. The SLF ascended as a holistic tool that considers not only income but also gender relations, social institutions, and property rights necessary to support a standard of living . It has been applied in various studies to examine the contextual and multi-dimensional nature of vulnerability . The framework has also proven beneficial for assessing the ability of households to withstand shocks . It highlighted that people need to possess basic tangible and intangible assets to successfully pursue different livelihood strategies . The possession and usability of assets, as described by the SLF, reveal differences in households’ recovery from disasters that could result from adaptation and livelihood resilience . The SLF looks at five types of “capitals,” for which there are wide and, for some capitals, contested literature about their definition and measurement. The capitals included in this framework are: human, social, financial, physical, and natural . The concept of capital implies the presence of usable productive resources. It is understood that all capitals are interdependent and interrelated . Capitals are not merely possessions but take three distinctive roles: a vehicle to make a living, a way to give meaning to that living, and a challenge to the structures under which people make a living . Human capital arises from the idea that nowadays humans are in charge of evolution and from the transformative effects of science and technology . Personal abilities, including education and health status, are used to measure human capital. Such capital may be the most important component of the framework , mainly because using some resources depends on an individual’s depth of knowledge and level of cognitive skills . Social capital comprises real-world links between groups or individuals that enhance networking. This capital contains features of social organization that can facilitate coordinated actions . It provides the adhesive which smooths co-operation, exchange, and innovation. However, social networks can also be a barrier that members use to exclude others and reinforce dominance or privilege. According to its effects, social capital can be divided into three categories: bonding, bridging, or linking . Social capital categorized as bonding comprises groups that tend to be homogeneous in terms of socioeconomic background. Due to the strong ties among the members, social capital in this sense can help the flow of information within the group, but it can also limit diversity . Social capital that functions as a bridge provides weaker connections among members who possess similar social standing but different backgrounds . However, this category provides a higher diversity of members. When ties between different economic and social classes exists, we can speak of linking social capital. This category aids poorer residents in obtaining information to which they did not have access within their own networks .

Compared to these human and social capitals, the last three capitals discussed in the SLF are more concrete. Financial capital refers to those assets that can be used to purchase other capitals. Physical capital represents the basic infrastructure and production equipment such as transportation, water systems, and energy. Natural capital comprises goods and services such as the type of soil, available land, and plant genetics.A single measure of vulnerability is not possible; therefore, the common approach for its quantification is through the creation of composite indices or indicator-based assessments . An indicator is an observed measure, qualitative or quantitative, that can help to simplify and explain a complex reality . A composite index aggregates several individual indicators to provide a single value that measures the multidimensional, complex, and meaningful issue of vulnerability . Plagued with a lack of consensus, an ideal methodology for the creation of a composite vulnerability index does not exist . Methods for doing so encompass uncertainty, subjectivity, and assumptions that should be recognized and made clear throughout the analysis . Such uncertainties should not be presented as a shortcoming but rather an ‘honest picture’ that stimulates the creation of policies that are flexible and adaptable . Before creating an index, however, a clear and compelling conceptual and theoretical framework for vulnerability needs to be developed. This first stage of this development should focus on exploring and evaluating approaches, fundamental concepts, and relevant theoretical frameworks for understanding vulnerability, as well as on conceptualizing the structure and composition of the complex system being analyzed . The vulnerable entity or system’s boundaries are typically difficult to define accurately. In part, this difficulty arises from the desire to measure the vulnerability of entire countries or complex systems. But even when the vulnerability assessment is restricted to a local scale, the system/entity interacts with a vast array of institutional, economic, political, and social contexts, which creates uncertain boundaries . After a conceptual framework is chosen, a well-defined spatial scale and scope of analysis is required. Applying an index to different spatial scales may result in different vulnerability patterns . Scale is related to the resolution that is available for the data. Although scale is important, however, selecting indicators to make up your index is a greater challenge in the vulnerability community. Indicators are useful in simplifying a system’s complexity, but as we have noted, they need to be used with caution when operationalizing vulnerability. Different approaches are taken to choosing indicators. Deductive arguments use a top-down approach to select indicators a-priori based on a theoretical framework. Inductive, bottom-up, approaches are data-based; they start with a larger set of indicators which are reduced by using either factor analysis or principal components analysis . This inductive approach is good for data reduction, but its subjectivity at critical stages contributes to uncertainty .

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Southeast Asia is currently the centre of the amphibian trade as food for human consumption

Regulations and restrictions on the amphibian pet trade would provide safer conditions for both humans and wildlife. These recommendations resonate well with ethics in civil societies around the world . For instance, following the implementation of the wildlife trade ban in China, a questionnaire was developed by Chinese conservation organisations to understand the public’s point of view. In urban environments the survey received over 100,000 responses with 96.4% supporting a ban on consumption of all wild animals, and over 90% supporting a ban of all trade in wild animals, including for food or medicinal use . In another survey conducted in March 2020, covering several eastern Asian regions , 93% of the 5000 respondents highlighted the same willingness to eliminate illegal and unregulated markets, with 82% of respondents wishing to do so because of fear of further zoonoses . Eastern Asia has therefore shown strong leadership following the current pandemic, the resultant increase in public awareness, and in synergy with the need for quick action to mitigate against further pandemics. However, in this region amphibian trade is not well regulated, amphibian species richness is poorly understood and most species are not nationally protected . For instance, only a small proportion of declining amphibian species are currently listed on CITES , yet the amphibian trade is a major cause of population declines in several species . In view of the global amphibian decline and the risks of zoonoses, we support the current wildlife trade bans, as well as measures to safeguard wildlife from over exploitation, and propose the following recommendations specifically for amphibians.Historically, much of the internationally traded amphibian meat originated in Bangladesh and India ,hydroponic vertical farming until the Indian bullfrog and the Indian green frog were included on Appendix II of CITES, and the trade of the species was banned in both countries due to the illegal and unsustainable capture of wild frogs .

The amphibian legal trade then shifted, primarily to Indonesia, and resulted in an increase from 180 million to 1 billion individual frogs of several species being traded between 1998 and 2007 . The principal importers for the food industry are the European Union and the United States of America , although the trade within the region is not negligible . The domestic harvest of native wild amphibians in the USA and France has already impacted amphibians through the loss of large populations of some species . These countries are now relying on imported frog meat that is generally not traceable . In addition, a significant proportion of the current amphibian trade for food and pets is unsustainable, likely to involve laundering of wild-caught specimens as captive-bred , and likely to spread batrachochytrids and other pathogens . An example of unsustainable trade is the mismatch between the quota set for the white-lipped tree frog by the Indonesian Captive Breeding Production Plan and the potential reproduction based on breeding biology of the species . However, the risks linked to trade need to be mitigated for some species, especially in Indonesia – the primary contributor to the amphibian trade. The Ministry of Agriculture and Rural Development of Vietnam ordered a ban on the trade of wildlife in March 2020, implemented in July by the Prime Minister , stipulating that wild animals and products thereof cannot be traded or consumed even when authorised by CITES permits. In addition, it recommends the closure of illegal wildlife markets, the improvement of wildlife farming management and the development of a database for threatened species currently in captivity . The ban has already resulted in several amphibian species being removed from the trade . However, this is a temporary measure with an extension being discussed , and specific licences for farmers can still be legally acquired. Nonetheless, this ban means that the sale of wild native East Asian bullfrogs has been discontinued in the country and the bullfrog populations may improve from a break in wild harvests . Furthermore, the environment may benefit from a decreased risk of pathogen transmission . If the trade ban is upheld, amphibians currently in captivity would likely need to be either euthanised or released.

While culling without financial subsidy is unlikely, these captive populations would probably be illegally sold or released into the wild, as seen in other species in similar situations . Similar to instances of individuals escaping from farms , the release of farmed amphibians can result in genetic homogenisation and the loss of genetic diversity across wild populations , as well as increasing the likelihood of pathogen transmission between released farmed stock and wild amphibians . Genetic homogenisation is a particularly salient problem in species complexes where cryptic species await formal description, such as H. rugulosusand Andrias spp. . Fortunately, in the case of H. rugulosus, frogs are generally harvested locally for the establishment of farms, therefore escape or release is unlikely to result in the introduction of individuals from segregated or different populations/ species that may threaten genetic integrity . Other native species have the potential to be locally farmed, such as Fejervarya cancrivora and Limnonectes macrodon in Southeast Asia , and Rana spp. in North East Asia, where amphibian farming relies on species that are better adapted to cooler climates . For instance, there were 152 farms breeding Rana in northeastern China in 2007 . In R Korea, farming of three Rana species has been permitted since 2005 , and several dozen facilities are now farming Rana species . While farming native species can sometimes be benign, the available numbers of captive-bred Rana are not currently satisfying the market . In R Korea, farms can apply for permits to import the same species as the one they breed, mostly from China . In China and Russia, this translates to illegal harvesting from the wild , smuggling , unsustainable export , and species laundering under the cover of farming following the significant depletion of wild populations . A complication for the amphibian meat trade arises when a farmed species is non-native, such as the American bullfrog . Multiple escapes and releases have resulted in feral populations of a highly invasive species becoming established in all eastern Asian countries where its ecological requirements are met .

The presence of L. catesbeianus has been linked to introduced pathogens and higher pathogen prevalence in native amphibians , as the species is a known reservoir of Batrachochytrium dendrobatidis , ranavirus and other parasites . The presence of the species outside of its range has been clearly linked to numerous declines in native species , and negative economic impacts when invasive populations are established . While upholding the trade ban in Vietnam has a strong conservation benefit for many native species, it may also result in the establishment of farms of invasive species, such as L. catesbeianus, and the establishment of invasive populations when farmed individuals release or escape. Similar issues have been expressed about the possibilities of other species becoming invasive. For instance, in the Philippines and in the Malaysian states of Sabah and Sarawak in Borneo, H. rugulosus is a non-native species commercially farmed for the food trade as well as for fishing bait and aquaculture feed , despite the climate of the area being adequate for invasions by the species . Additionally, Chinese giant salamanders that were released in Japan after being farmed for food, now hybridise with the native Japanese giant salamanders and threaten their genetic integrity . Consequently,vertical agriculture we recommend upholding trade bans, especially for live individuals and threatened species. While farming of L. catesbeianus has not been as successful as expected in some countries, such as Indonesia and the R Korea , it is still a widespread practice in some other regions , and escapees from farms in all regions continue to threaten the surrounding wildlife. Farming of native frogs has also been developed into a lucrative business , with Hoplobatrachus spp. individuals reaching marketable size within four months . For comparison, L. catesbeianus takes up to three years in natural weather conditions around 40◦N, or eight months at 25–30 ◦C . Areas with a tropical climate can profitably farm H. rugulosus or Fejervarya spp., especially given that some of these species are considered to be delicacies in some regions . Colder areas can rely on Rana spp., where research shows that the farming of R. chensinensis and R. dybowskii can be profitable and where it is now relatively prevalent . However, the current farming of native species cannot be treated as a net-positive conservation intervention. For instance, harvesters in Indonesia believe that harvested species are declining, although an alternative explanation is competition between harvesters . Similarly, populations of the native H. rugulosus in China have declined by approximately 30% between the 1980s and 2010s , and other large-bodied frog species have declined in Southeast Asia during the last decades . In addition, the genus Rana has declined over 60 to 70% of its range despite the active development of amphibian farming in China, resulting in a 21.5% decrease in populations of Rana over 15 years , on par with the decline in Rana populations in Russia . Breeding of these species in farms has not decreased the intensity of harvesting in the wild , and it is therefore important that the farming of native species starts supporting conservation efforts by relieving pressure on wild populations and that these operations cease the laundering of individuals and contributing to the decline and extirpation of wild populations.

Therefore, we recommend a complete ban on the farming of nonnative amphibian species, especially when there is a high potential for feral populations of such species to become established in the environment surrounding the farm, i.e. non-native species to become naturalised. In the absence of alternatives, and when possible and ecologically sustainable, non-native species should be replaced by local native species. A certification system to trace the provenance and source of animals by both sellers and buyers, as used in fisheries, could help identify and curb illegal wild harvests; however, clear mechanisms to prevent fraud are also needed . Alternatively, regulated harvest of wild populations could still be allowed at specific times of the year and in specific contexts, such as rice fields, as these are the primary habitat of numerous common and non-threatened Asian anuran species . Considering this, rice fields would require protection, as an increasingly high number of rice fields are being developed for non-agricultural uses, especially in northern Asia . Finally, it would be important to give consideration to rectifying the negative impact of farming non-native species, such as the local eradication of feral populations of L. catesbeianus, already planned by some nations , following precedents set elsewhere . Amphibian pathogens are spread and introduced through the wildlife trade , and the pet trade is known to be a significant pathway for the spread of amphibian pathogens . In addition, the pet trade threaten species and may result in the introduction of feral populations, and while no such species has been reported in Asia, to our knowledge, potentially invasive species have been found in the wild, such as Xenopus laevis in R Korea following release or escape . Another amphibian invasion related to the trade is Polypedates megacephalus, which was introduced at several localities with horticultural plants, and the populations have been increasing ever since . However, international trade is not the only problem, and trade of species between provinces of a country with different species assemblages results in the same loss. Southeast Asia is a hub for international amphibian trade, and this has a critical impact on threatened species . As a result, several species in the region have exhibited declines in population sizes and have been locally extirpated . Specifically, the pet trade is now the primary threat to some Southeast Asian newts, with the USA the largest importer until recently . An example is the Lao warty newt in Lao People’s Democratic Republic, where collection for the pet trade is a principal driver for the species’ decline . Villagers relied on the sale of 100 individuals to European, Japanese, and Chinese collectors in 2008 and 2009, an unsustainable number for the species .

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The activities of urban farms fall naturally under definitions and descriptions of agroecology

It also serves to reaffirm cultural identity and a sense of place for immigrant and refugee families. Agroecology places a strong emphasis on human and social values, such as dignity, equity, inclusion and justice contributing to improved livelihoods of [urban] communities . Our study demonstrated that the majority of farm respondents placed food security, education, and environmental sustainability above profit, sales and yield. Forty percent of respondents self-identified as “Educational” farms, and most others offer educational workshops and demonstrations as part of their focus on horizontal knowledge-sharing. Agroecology seeks to address gender inequalities by creating opportunities for women. The majority of our study respondents were also women. As a grassroots movement, urban agroecology can empower women to become their own agents of change.Our results suggest the opportunity to reconceptualize and refocus the urban food policy discussion in U.S. cities around urban agriculture in a way that includes and values their social, educational, and cultural services. Urban farms are recreational and cultural heritage sites bearing comparison to public parks and museums, while also producing invaluable healthy food in areas that most need it. They provide important respite, social connection, and stress reduction to urban residents, often particularly in need of peaceful spaces. In the words of one farmer, “Urban farms can be havens of peace, health, and community, but it requires heavy involvement and advocacy from those communities for the long term in order to be successful” . Agroecology calls for responsible and effective governance to support the transition to just, equitable and sustainable food and farming systems. In an urban environment, this requires the creation of enabling policies that ensure equitable land access and producer control over access to land, especially among the more vulnerable and historically marginalized populations. Land access is expressed most frequently as an obstacle to scaling urban food production by survey respondents, and it is certainly more of a challenge for lower-income and minority groups interested in cultivating their own “commons” . There are examples among our East Bay survey respondents of collective governance at the farm and community level, such as one farm site which is owned cooperatively by three non-profit organizations that collectively serve minority and formerly incarcerated populations,cannabis grow facility layout aspiring beginning farmers, and the local community through a cooperative goat dairy, fruit tree nursery, and annual vegetable production plots.

City and county governance bodies have an opportunity to strengthen the resilience of urban agriculture operations and opportunities for farmer collaboration by providing subsidies and incentives for social and ecosystem services. City-level efforts to compensate or recognize farmers for ecosystem services such as soil remediation and carbon sequestration, for example, are not yet realized. Further examples of responsible governance from our data include recommendations for public procurement programs to source food from aggregated urban produce . Our respondents are engaged in circular and solidarity economies, key features of agroecology, including bartering, sharing, and exchanging resources and produce with those in their social networks. They are also interested in collaborating in a localized effort to strengthen the link between producers and consumers by aggregating produce and sharing distribution . As cities work to fulfill their role in providing basic services to citizens, farmers are pointing out an important opportunity to provide refrigerated transportation, storage, and organizational infrastructure to transfer all possible produce grown on urban farms to the best distribution sites. Communication platforms, transport systems, and streamlined procurement in this arena following from other regional “food hub” models could improve the landscape for urban food distribution dramatically . All urban farm respondents are also engaged in closed-loop waste cycles: through composting all farm waste onsite and collecting food scraps from local businesses, farms are involved in a process of regeneration, from food debris to soil.Through extending the UAE framework from farms to urban policy and planning conversations, more efficient pathways for addressing food insecurity in part through strategic centers of urban production and distribution can emerge in cities of the East Bay and elsewhere in the United States. Finally, agroecology relies on the co-creation and sharing of knowledge. Top-down models of food system transformation have had little success. Urban planners have an opportunity to address food insecurity and other urban food system challenges including production, consumption, waste management and recycling by co-creating solutions with urban farmers through participatory processes and investing in community-led solutions. In our systematic review of the literature on whether urban agriculture improves urban food security, we found three key factors mediating the effect of UA on food security: the economic realities of achieving an economically viable urban farm, the role of city policy and planning, and the importance of civic engagement in the urban food system .

A radical transformation toward a more equitable, sustainable and just urban food system will require more responsible governance and investment in UA as a public good, that is driven by active community engagement and advocacy. We believe that urban agroecology principles provide an effective framework to capture the multiple ecological, social, economic and political dimensions of urban farming, beyond yield and profits, enabling those seeking transformative food systems change in the U.S. in the U.S. a common language and opportunity to measure and communicate more clearly the multiple benefits worthy of public investment. Framing this work as urban agroecology values the knowledge creation, community building, and human well-being that are also products of urban food initiatives. Our data illustrates how urban food sites are spaces of vibrant civic engagement and food literacy development yet remain undervalued by city planners and under constant threat of conversion as well as pressures of gentrification. With the majority of operations in our study functioning as non-profits, it is questionable whether many urban farms would actually be considered a true “agricultural” operation per the USDA definition as a majority of farms earn less than $1,000 in sales annually. As such, they are largely ineligible to apply for funding or loans from many of the federal and state agencies or granting programs such as the Farm Service Agency or NRCS. The idea that the UAE framework can illuminate multiple and often hidden sociopolitical dimensions of urban food production sites is powerful. For example, over 75% of urban farming sites in our study came into being for a multitude of reasons: including re-establishing justice and dignity into historically neglected and marginalized urban communities, fighting poverty, resisting the environmentally extractive, exploitative, racist, and obesity-inducing industrial farming system, reclaiming the ability to be self-sufficient and work with your hands, and re-educating society about the physical and emotional value of cultivating the Earth. Urban farmers aspire to many things: affirming a human right to healthy food, a food literate civil society,grow rack land tenure arrangements that favor socially beneficial rather than profit-maximizing land uses, and alternative forms of exchange and value creation outside the capitalist political economy. The term “agroecology” locates these values in a historical network of similar efforts to transform the global food system along socially just and ecologically resilient lines.

Reframing UA through the lens of UAE can ultimately help U.S. policy makers and city planners better understand and support urban agroecological endeavors, and provide researchers, urban citizens and urban food producers a more inclusive mode of inquiry that can lead to transformative food system change, taking care not to dismantle, invalidate, or eliminate the revolutionary, anti-oppression elements through overly prescriptive “policy solutions.” When it comes to researching, documenting, and advancing transitions to sustainable food systems through agroecology, the urban context is an important one to consider, given the growing percentage of the global population living in cities. We acknowledge Gliessman’s call for applications of his “5 levels of food systems change,” showing in our data how East Bay urban farmers are endeavoring to scale up to Level 5: “build a new global food system, based on equity, participation, democracy, and justice, that is not only sustainable but helps restore and protect earth’s life support systems upon which we all depend” . We encourage future engaged scholarship in the U.S. that employs a UAE framework to ask and answer important remaining questions about the transition to sustainable food systems, in partnership with urban farmers, around valuation, preservation, and connectivity of diversified food production sites in the modern city. The realities of climate change, both already experienced and forecast for the future, make teaching young people about the causes, consequences and solutions to climate change a national imperative for public and private education. Climate mitigating action is needed at all levels, from international to individual. Current levels of awareness and knowledge about climate change are “insufficient in leading to effective behavioral change” . Leaders in climate change education argue that “based on carefully developed evidence, the emissions gap cannot be closed without also closing the education gap—that is, the gap between the science and society’s understanding of climate change, the threats it poses, and the energy transition it demands” . Effective climate change education practices are badly needed to close the gap, as authors go on to state, “education for action requires more than scientific literacy; it must integrate concepts and dynamics across disciplines and in ways that address affective, social, and cultural forces—a challenge that can be met through effective and evidence based climate change education” . As a whole, the Lowell middle school demonstrated much higher levels of knowledge and engagement around climate change than the average American teenager or adult. Based on a 2010 nationally representative survey of American teenagers, knowledge of climate science basic facts was found to be very low . 59% of American adults fall into the “Alarmed” or “Concerned” categories of the YPCCC Six Americas spectrum as of December 2018 compared to 82% of Lowell middle school students.

What remains a challenge both nationally and at Lowell is building optimism around our ability to solve climate change: only 8% of youth agreed that we can and will do something to mitigate climate change in a recent study , and a mere 5% of Lowell students indicated they believe their generation will solve climate change. While acknowledging the receptive audience for implementing the curriculum, the results relating to increased student engagement, increased reading scores and favorable response to a humanities-focused climate curriculum are nevertheless significant and worth building on as an approach to middle school climate education. Further hypotheses are generated such as the claim that climate change as an engaging topic can help boost student performance in core academic disciplines , requiring further testing via controlled experiments. The time period between 6th and 8th grade is a significant youth development stage during which students develop capacity in knowledge retention and empathy and gain exposure to many new topics, and yet the 6th graders performed equal to or above the 8th graders on most climate knowledge and engagement questions. They shared information learned with families and friends more often than their 8th grade peers learning about climate change through science only, generating important hypotheses for CCE/IGL scholars . Results and best practices from this case study should be applied intentionally to other classrooms and school contexts. The web of support is a crucial enabling factor as well as the participation of key influencers, which must be identified in other contexts. The Lowell School curriculum coordinator suggests several vehicles for integrating similar curricula into more structured, state-mandated public school subject matter: through choice of reading materials in civics classes, suggested options for student independent research projects, and current events classes at the high school level. She outlines three specific opportunities for incorporating climate education into social studies classrooms through tweaks to what is already happening, rather than major curriculum overhauls: 1) in elementary school states and regions studies, where studying the climate of the state or region is already an explicit objective, 2) middle school global geography classes, and 3) in high school current events classes. She sees these as opportunities to “lean into the climate change challenges and how people are addressing them in different contexts” , while minimizing instructional tradeoffs. The Director concurs, adding, “for independent schools this change is very easy. But for public schools, there’s so much you can do with this curriculum too. If you have to teach about government, geography, or history you can use pieces of this [integrated into pre-existing units and curriculum mandates]” .

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